Separation Methods for Waste and Environmental Applications (Environmental Science & Pollution)

SEPARATION

METHODS

FOR WASTE AND

ENVIRONMENTAL APPLI CAT^ oN s

JACKS. WATSON Oak Ridge National Laboratory Oak Ridge, Tennessee

M A R C E L

MARCEL DEKKER, INC. D E K K E R

NEWYORK BASEL

This Page Intentionally Left Blank

ISBN: 0-8247-9943-7 This book is printed o n acid-free paper.

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Copyright 0 1999 by Marcel Dekker, Inc. AU Rights Reserved. Neither this book nor any part may be reproduced or transmitted in any form or by any means, electronic or mechanical, including photocopying, microfilming, and recording, or by any information storage and retrieval system, without permission in writing from the publisher. Current printing (last digit): 1 0 9 8 7 6 5 4 3 2 1

PRINTED IN THE UNITED STATES OF AMERICA

To my wife Patricia whose patience and encouragement heIped me to complete this work

Preface

The purpose of this book is to bring together information and concepts needed by those concerned with selection and/or design of separation process equipment for treating wastes or environmental streams. In treating a waste stream or a contaminated portion of the environment there are usually only two or three options: separation of the contaminant from the stream of material, destruction of the contaminant, or isolation of the material to prevent its release or spread in the environment. Separation processes are often the best choice, but their roles may not be obvious because these processes are sometimes called by different names such as removal of contaminants, concentratfon of contaminants, orpurfficatfon of waste material. These terms all refer to separation processes. Enriching, stripping, clarflcatfon,and benefication are a few of the additional terms used to describe separation processes, but they have come to have more specific meanings. It hardly seems necessary to explain how or why treatment of waste streams and contaminated soils or groundwater has become a topic of increasing concern and importance. The past few decades have seen a growing awareness of the important effect of environmental pollution on the health of people, plants, and animals. This increased awareness was generated, in part, by individuals, by organizations such as the Sierra Club, and by popular publications such as The Silent Sprfng.The concern has generated a large increase in research on the effects of chemicals and other pollutants on both our health and the health of the environment. This research on environmental effects made industry, the government, and the technical community more aware of the impact of many waste effluents o n the environment, and the understanding of this impact has reached the public at large. Many chemicals and materials that were in common use only a decade or so ago are now known to be hazardous, and in some cases, the manufacture of those materials has ceased or V

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PREFACE

is scheduled to cease. The list of known toxic substances has grown significantly during this period. This increased research and identification of more toxic materials has also increased the concern of the public, and that has stimulated additional research. Despite the increased recognized risk and the tighter regulations, it is often necessary to use hazardous materials. Although the use of hazardous materials makes industrial operations more difficult and more costly, it is possible to operate industrial systems safely using hazardous materials without releasing significant quantities of toxic wastes, and industrial firms are learning to d o just that. Use of a toxic material does not have to be equated with release of significant quantities of that material. However, industrial and consumer activities in the past, when less effective containment methods were used, have left us with a legacy of contaminated soil, buildings, equipment, etc.; this legacy has had a negative effect on public confidence in some companies, and even some entire industries. This legacy of hazardous materials must be handled when “remediating” sites. There is a need for better ways to both handle and contain hazardous materials during current operations and to remove contaminants from water, soil, equipment, and anywhere contamination from past operations has spread. Separation methods play important roles in solving all of these problems, and their roles are expected to increase. Although enormous sums have been spent on contaminated sites during the past decade, the number of sites that have been completely remediated has been disappointing to many To accelerate the remediation of contaminated sites, it will be necessary to utilize the most cost-effective methods. It is important that those working on cleaning up environmental problems and designing or modifying process systems to reduce future spreading of hazardous contamination be well versed in most aspects of separation methods, including the selection of the best methods for a problem, the best way to apply methods, and the limitations of each method. This book is an effort to help with these needs. Separation Methods for Waste and Environmental Applications The separation methods that are or are likely to become most important in solving waste and environmental problems include a number of chemical and physical separation methods that have traditionally not been covered in any one university curriculum or in a single textbook. Since this book is aimed at applications in a small, but rapidly growing, segment of the process industries-the waste and environmental industries-coverage

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vii

is based on the importance of the methods to this segment. Separation methods for any application should be based on the problem to be solved and not influenced by limitations in the background of the engineer or others assigned to solve the problem. Most separation processes are concerned directly with meeting regulations or discharge limits, mostly for water and air. The processes are also important in meeting solid waste disposal regulations, especially those involving the concentration of contaminants in the solid waste. Separations can also be used in other, earlier, parts of a process system to prevent pollutants from reaching the effluent streams. For instance, pollutants that result from undesired components in the feed stream could be removed from the feed stream as well as from the effluent stream. It is common practice to remove hydrogen sulfide from natural gas so it will not enter the environment when the gas is burned or processed in any other way (usually to make “syngas”). This book focuses principally on removal of contaminants from effluent streams, but the examples include several cases in which separation systems can be applied elsewhere to meet the same regulations. Potential Readers

The complexity of the material in this book varies, but most of it should be understandable to graduate engineers or scientists, graduate students, and upper-division undergraduate students. N o exceptional mathematics background is required, and most of the subjects covered are not exceptionally complex. A basic understanding of general chemistry is needed to understand many sections, but most engineers and scientists working on environmental problems should have a year, or more, of undergraduate study in chemistry. Attempts are made in the book to explain the few concepts that are less likely to be covered in basic chemistry courses. Those who will be most interested in the material are environmental engineers, chemical engineers, and other engineers and scientists who have some experience in the field, and they will probably have more than basic understanding of the chemical concepts needed. A brief discussion of the chemistry involved in a concept is sometimes presented, but this is not principally a chemistry book. In most cases, the additional details may not be absolutely necessary to use the concepts presented. This book is intended to be used by some readers to review separation methods and by others to become acquainted with methods with which they are not sufficiently familiar. Civil and environmental engineering textbooks cover some of the same topics, but the coverage is usually different. In most respects the organization is more like that of a chemi-

Viii

PREFACE

cal engineering book, with the focus on individual separation processes, and the treatments of water and air streams using the same separation principles are discussed together. Information on the separation methods most important in environmental and waste problems is emphasized. There is also an attempt to provide insight into the concepts and principles that must be understood for selection of separation methods for new problems. Traditional books on separations for chemical engineers usually describe each separation method well but d o not give much attention to comparison of the different methods. That is partially because the traditional books d o not focus on a constrained group of applicationsenvironmental and waste problems-and such comparisons would be difficult to make for a wider group of applications. Of course, even for the relatively narrow range of applications in this book, judgment is often needed until detailed performance and economic studies are completed. Nevertheless, at least the introduction to selective criteria is expected to be helpful to the readers. The general comparisons are intended to guide the reader by suggesting which separation methods should be considered for a given application and conditions, not as a final judgment on which method to use. Separation processes are usually a strong part of chemical engineering practice, and chemical engineering textbooks probably provide more information on fundamentals of separation processes than books written for other fields. Because the chemical and process industries are involved in such a wide variety of materials, there is less temptation to seek a few approaches that will satisfy most separation needs than one might find in books for fields with less varied needs. This book is also expected to be useful to the trained chemical engineer because it differs significantly from most chemical engineering books by including more detail on separation methods important in waste and environmental treatment.

Differences Between This Book and Most Separation Texts The strong focus on separation methods for waste and environmental treatment is intentional. The most obvious sign of this focus is probably in the examples given, which are mostly drawn from environmental or waste problems. However, the most important aspect of the focus is reflected in the selection of the separation methods covered and the space devoted to each separation method. This is most evident when one compares the topics and the space allotted to each topic with the coverage in other separation books. This is important because many separation methods that are important in environmental and waste problems are not covered

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ix

extensively in standard separations texts, usually texts aimed at chemical engineers working in the process industries; this is especially notable in texts used at the undergraduate level. Of course, the selection of the methods to emphasize in this book comes from my own experiences and views. The career of each engineer or scientist working on waste and environmental problems is different; so there can be no claim that this book is custom-tailored for every engineer and scientist in the field. The reader will find adsorption covered in far more detail than in separation texts that attempt to cover all separation methods. Adsorption is especially important for removing the last traces of contaminants from both aqueous and air effluents. Adsorption can be the principal method for removing a contaminant or it can be a “polishing” method for removing traces of contaminants after other methods have been used to remove the bulk of the contaminants. Other separation methods that are especially important for waste treatment are gas absorption and gas stripping. Some separation methods are covered in more detail in this book than they have been covered in most “classic” texts on separations because of their high potential for future applications in waste and environmental processing. Perhaps the most notable example is membrane separations. Applications for membranes are currently growing rapidly, and this growth is not limited to waste and environmental applications. The chapter on membrane processes focuses on reverse osmosis and removal of hydrophobic contaminants from effluent water and/or air emissions rather than on some of the other exciting new applications of membranes in gas separations. A similar focused (or limited) treatment is given for liquid-liquid (solvent) extraction. Although the inherent solubility and entrainment that occur in all liquid-liquid extraction systems introduce traces of organic compounds to the treated stream that could be considered a second contaminant, there are places where liquid-liquid extraction can remove some contaminants more effectively than other methods. The removal of metal ion contaminants from aqueous solutions is a notable example. The chapter on liquid-liquid extraction thus focuses on systems in which a highly insoluble extractant can be used, and especially on the removal of metal ion contaminants. The most important separation method in the process industries is distillation, which involves, by far, the largest capital investment and energy consumption of any separation method. Despite its great importance to the process industries, distillation is not given prominent treatment in this book, principally because it is not expected to have such great importance in waste and environmental problems. A chapter is devoted to distillation because it can still be important in some waste and environ-

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PREFACE

mental applications, but readers familiar with other separation texts are likely to find the treatment of distillation more brief and less detailed than they expected. Distillation is generally most useful in recovering products at higher concentrations than those usually found in waste and environmental problems. Crystallization is another separation method that is covered in less detail than one may find in other separation texts. There is no separate chapter on crystallization, but some aspects of crystallization are included in several chapters. Many aspects of crystallization, such as the slow growth of crystals to produce high-quality and relatively pure crystal products, are not likely to be issues in waste and environmental operations, which are far more likely to deal with very dilute solutions. However, precipitation is simply another name for crystallization, a name that is more likely used with “crystallization” of highly insoluble materials, usually initiated by a change in pH or concentration of a reactant. Precipitation of insoluble materials is discussed along with adsorption of contaminant on precipitants (or incorporation of contaminants into precipitants) and the removal of precipitants from solutions. However, these are rapid “crystallization” operations in which the principal interest is in the chemistry to form highly insoluble components and remove the precipitated solids. When the precipitated solids have extremely low solubilities, it is less likely that the crystal growth can be controlled very well, and that is usually not a key goal of waste/environmental precipitation operations. Readers who are familiar with other separations texts will also note a stronger emphasis on physical separations such as filtration and sedimentation. Physical separations are often covered in separate texts from chemical separations. Here they are covered with chemical separations, because they are already important in waste and environmental systems, and their importance is expected to grow. Filtration and sedimentation are well established and used almost universally, because almost all waste and groundwater contain solids that must be removed. Even if the solids are not contaminants (there are limits on solids in discharge waters), they often adsorb “soluble” contaminants, and discharge limits often cannot be met without removal of the majority of the solids. Solid-fluidseparations are also often required in chemical separation systems because so many chemical separations cannot function well in the presence of high solids concentrations. Filtration is usually required on any fluid stream going to adsorption or other packed-bed separation equipment; so it is needed even when it does not remove a contaminant. Filtration and sedimentation are also important steps in precipitation processes, and the physical separations may be the most difficult aspect of such systems.

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Other physical separation methods that currently play some, but limited, roles in waste and environmental separations are believed to have potential for increased importance in future waste and environmental treatment systems, and those methods are discussed at least briefly. The coverage is largely descriptive rather than quantitative. These methods are grouped together into a single chapter. The reader should have some familiarity with these methods, but their current importance does not warrant more than the brief summaries given in this book.

Descriptions of Design Procedures

All the major chapters on separation methods that are expected to be most important to waste and environmental problems include at least some discussion of the science involved in the separation method and design procedures that allow the reader to size equipment or to estimate the performance of given equipment. Throughout these chapters, the reader is reminded that computer packages are available that perform many of the calculations described. However, it is important that the reader understand what is going on in such calculations. There are assumptions and limitations in all such calculations that users should understand. Also, in some cases it is as easy to do calculations manually as it is to set them up for the computer. The descriptions focus on relatively simple cases because they aim to provide insight into the design method; often the insight into the simpler cases is all that is needed to understand the principles that are used in the more complicated cases that almost certainly should be evaluated using powerful computer codes and packaged computer analyses. Essentially all the design procedures given in this book are available in standard textbooks on separations. The only significant exception is the description of a generalized approach to design of adsorption beds with constant pattern breakthrough curves, and even this approach is based on principles that are dispersed throughout other textbooks. The unique feature of this book is the inclusion of the particular collection of methods presented. Thus, one would need to look at several texts to find the information presented here, but in looking at several texts, one would find far more detail on some separation methods, perhaps more detail than was wanted or than would be needed. Example Applications Example applications are usually given in the major chapters in two places. Early in each major chapter there is a brief mention of a few of the most

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PREFACE

important general classes of the method, giving an immediate sense of how a separation method could be used to address a waste or environmental problem. However, most examples are presented near the end of the chapter, usually following a general description of conditions that make the method appropriate for a particular application. There is no practical way to include all applications that could be of interest, so those given should be viewed only as examples. Some of the most important applications are mentioned, but most are simply interesting. There are applications that include combinations of separations and applications that are only under study and could be important in the future. In some cases, the applications are mentioned because they illustrate a point about conditions that make a particular separation method attractive. The lists of applications are not complete. That would be impractical because of the constant generation of new ideas and new applications for separation methods.

Jack S. Watson

Contents

iii

Preface

1

1. Introduction

23

2. Adsorption and Ion Exchange

3. Absorption and Stripping

167

4. Membrane Processes

253

5. LeachingExtraction

347

6. Liquid-Liquid Extraction

383

7. Distillation, Evaporation, and Steam Stripping

413

8. Surface Filters

46 1

9. Deep Bed Filters

497

10. Sedimentation and Settling

527

11. Precipitation

551

12. Other Physical Separation Methods

563 595

Index

xiii

1 Introduction The treatment of industrial wastes and contaminated soils and groundwater is a rapidly growing industry in itself and now consumes a substantial portion of the activity of many firms. Several new firms have been organized during the last two decades whose business is dedicated entirely or largely to solving waste and environmental problems. Some of these firms are now large and have operations throughout the United States and even overseas. Although the rate of growth of this industry appears to have slowed in the last few years, it is still significant and appears to be significantly higher than the growth of industry as a whole. There has been a accompanying increase in interest in the academic community in environmental issues and research on ways to treat environmental problems. Ecology programs and environmental engineering programs have grown greatly on many campuses, and environmental activities have become important parts of other academic programs from engineering to law and business. This increase in activity and business concerned with environmental and waste problems has resulted from the increased awareness of the public to the hazards of many industrial wastes. Research during the last few decades illustrates the importance of pollution in air, water, and soil to the public health and to environmental quality. The results of these studies have raised the public awareness and concern with industrial pollution, and the public concern has resulted in new regulations that affect waste and environmental treatment. Environmental problems such as acute spills or gradual environmental damage have been recognized by the press and electronic media to be of interest to the public, and this has enhanced the rate at which environmental news reaches the general public. The increased awareness and importance of environmental issues have not escaped the attention of lawmakers and regulators. Essentially 1

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everyone is aware of the great increase in laws and regulations that have come into effect during recent years. This growth in regulations was crowned by the formation of a major agency, the Environmental Protection Agency (EPA), and the formation of related programs within other federal agencies. Every state has its own state version of the EPA, and in some cases the regulations from the state agencies have been stricter than those from the EPA. This increased regulation of environmental problems and issues has not been limited to the United States; essentially every country has set up similar environmental agencies, and in some cases the laws or enforcement is even stricter than in the United States. The changes in the regulatory environment during the past two decades have greatly affected most industrial operations. Almost everyone who has worked in an industrial company has seen these changes, and when hazardous materials are involved in industrial operations, the changes can be profound. These three changes-in our awareness of the seriousness of environmental problems, in new research on environmental and health problems, and in environmental regulations-are closely connected; the activities in each area have increased because of results from the other changes. Despite some newer voices in Congress with complaints about federal environmental regulations, it appears more likely that improved understanding of the effects of industrial emissions on the population and the environment will continue to require strict regulation, perhaps in some cases regulations even stricter than those currently in place. The recent history of environmental regulation has shown an almost continuous reduction in discharge limits allowed for a growing number of materials. Although it would be simplistic to expect the regulations to continue to be tightened at the same rate forever, there is still a reasonable expectation that environmental regulations will continue to become more restrictive during the coming decades, but perhaps at a less rapid pace. There are powerful forces currently attempting to reduce the burden (or effectiveness) of some regulations that seem (to them) to be very costly and to play few roles in protecting the public or the environment. There also are clear cases where significant parts of the public object to environmental regulations, usually because the regulations or their enforcement affect or threaten jobs, but there is little evidence that the general public favors a significant reduction in environmental regulations or enforcement. Fear of hazardous materials and wastes appears to still be strong in the general public, and a significant relaxation in regulations does not appear to be likely as long as that fear remains. Current complaints are focused on some of the regulations and regulatory practices that appear to be least justified, especially the liability regulations that hold each con-

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tributor to a contaminated site potentially liable for remediation of the entire site. However, there is no reason to expect a major pullback of regulations except in these few specific areas where regulations may have been applied incorrectly. Overall the environmental regulations may continue to become stricter, hopefully in ways that will improve health and environmental quality efficiently as well as effectively.Waste treatment and environmental restoration is now a large industry in the United States and is still growing rapidly with expectations for considerable future growth.

SEPARATION PROCESSES IN WASTE AND ENVIRONMENTAL TREATMENT Separation operations are currently important in almost every aspect of waste and environmental treatment, but the separation treatment methods may go under other related names. These names include “removal” of a contaminant, “decontamination” of a material or effluent stream, “concentration” of a contaminant, “purification,” etc. There are generally only three options that can be used to treat waste or environmental streams: separation, destruction (reaction), or immobilization. Of course, in many systems, all three options can be and are used. A stream of waste materials could be treated by each option for remediation problems associated with different contaminants. Separations could be used to concentrate contaminants for eventual destruction or immobilization and to remove contaminants and concentrate or purify them to the point where they can be used again and no longer be considered “contaminants.” The reduction or elimination of waste streams is likely to become an increasingly important aspect of environmental protection; so one should not think of waste treatment entirely in terms of treatment of effluent streams. The addition of process systems to reduce toxic emissions from existing industrial facilities is currently the principal focus of waste and processing, and that is also the principal focus of the illustrations in this book. However, one should be prepared to view waste problems in a more global manner, including modifications to the industrial operations themselves to produce less waste and to utilize more of the wastes that must be produced. This projected shift in waste treatment techniques is one reason why readers are encouraged to seek a general understanding of the separation methods themselves and not focus too strongly on individual applications that could become less important in the future. Applications of separation methods are expected to increase as efforts are made to reduce waste volumes, reuse contaminants rather than discharg ing them, to reduce the concentration of contaminants in inlet streams

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CHAPTER 7

even further, or to remove contaminants from soils and groundwater. If the future approaches to waste management involve a greater emphasis on changes in the manufacturing processes and rely less on effluent treatment, the role of separations is not expected to decline significantly, but the roles of separations could shift. “GREEN MANUFACTURING”

There has been considerable interest lately in “green manufacturing.” One “driving force” for seeking green manufacturing is the Pollution Prevention Act of 1990 [l].The term “green manufacturing” can have different meaning to different people. In some cases, it can mean manufacturing with zero or minimal release of toxic materials. Note that the call may be for zero release, but “zero” may not have the meaning in these cases that some people may intend. It can simply mean that the presence of the toxic material is not detected; so better chemical analyses could change this meaning of the term. Of course, in the ultimate sense, if we had suitable chemical analyses, we probably could detect a molecule or a few molecules of essentially anything in any waste, product, or emission. Thus the practical definition of green manufacturing would spec@ that the emissions would be acceptable (within specified limits) and minimized. That is, one would reduce the emissions to levels as far below the accepted limits as possible or as practical (again another chance to hold different definitions of the term), Others define green manufacturing as minimizing or eliminating the use of toxic materials as raw materials or intermediates in manufacturing. Although one can argue that only the emissions count and that consumed or recycled intermediates d o not contribute to environmental pollution, a case can also be made for minimizing the presence of the toxic material where ever possible. Even the use of toxic materials leaves the possibility that there will be accidental releases, and the absence of toxic materials eliminates the possibilities that there will be toxic releases, either accidental or undetected. There is also the advantage that eliminating the use of toxic substances will eliminate the exposure of workers to those materials, even if the toxic materials are not released. This seems to be one common definition used in recent workshops and publications on the subject. The major concern is usually the use of chlorine and chlorine compounds in the synthesis of organic chemicals. These processes leave the possibility for release of some of the organic intermediates and for formation of trace quantities of other toxic compounds, such as dioxins. Intermediates such as isocynates are also targets

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for elimination. There have even been calls by a few people for total elimination of chlorine in chemical manufacturing. A total elimination of chlorine would be difficult and would eliminate the production of many useful products, including important pharmaceutical products. A general discussion of the subject can be found in a brief article by Browner [ 21. An example of the results of workshops and technical session can be found in the proceedings of a symposium on clean chemical manufacturing organized by the American Chemical Society [ 31. Since most of the separation processes discussed in this book are concerned with removing toxic or other materials from solid, liquid, or gaseous wastes, it may appear that separation methods are concerned with the more conventional approaches of using or producing toxic compounds but trapping the toxic components so that they cannot reach the environment, In most cases, that is a correct assessment. Increased use of green manufacturing would eliminate the presence of toxic materials in many waste streams and the subsequent need for separation methods. As desirable as these approaches are, they are not expected to eliminate or even reduce the growth in the need for more and better separation methods. There are several reasons why separation methods will remain among the primary tools in reducing pollution of the environment. Although a reduction of the use of toxic components in the manufacture of nontoxic products will be appropriate and is expected, the total elimination of the use of toxic intermediates is not expected. Note that several “useful” products are toxic, and to eliminate those toxic materials would eliminate the products themselves. Most insecticides and herbicides are toxic, at least slightly, to humans or the environment to a limited (but accepted) degree. Rather than eliminate these products, the public is likely to call for more restricted uses of these materials and the development of less toxic alternatives where uses are necessary. Operations that handle highly toxic materials are increasingly likely to require separations equipment on the off-gas and ventilation systems to prevent release of contaminants during accidental or normal operating conditions. Finally, one should note that there have already been significant “spills” or releases of toxic materials, and continuing efforts are needed to remove the contaminants from the environment. All of these activities are likely to require separations operations to provide better containment of the toxic materials that truly need to be produced and/or used and to decontaminate soil, water, equipment, and buildings that have been contaminated by earlier operations. To this author, the need to increase the use of separations operations for waste and environmental problems is likely to develop more quickly than the ability to decrease the use of toxic materials.

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CHAPTER 7

ENVIRONMENTAL REGULATIONS Because the regulatory restrictions are currently being assessed by Congress and regulatory agencies, and the approaches to regulations may be changed in the near future, a detailed description of the regulations will not be given here. Even if the approach to regulations is changed, the need for reducing the release of contaminants is likely to continue, perhaps with no more than selected limited changes in the allowable release of selected contaminants. Numerous laws are concerned with the release and disposal of contaminants, including the Research Conservation and Recovery Act (RCRA) which regulates the storage and disposal of solid wastes, the Clean Air Act (CAA), the Clean Water Act (CWA), and the subsequent amendments to these acts. Government facilities are also covered by the National Environmental Protection Act (NEPA), and some sites and facilities are covered by the “Superfund” laws. Those facilities dealing with radioactive wastes (hospitals, universities, electric utility companies, and many industrial concerns, as well as the Department of Energy facilities, etc.) must also deal with the Atomic Energy Act and regulations from the Nuclear Regulatory Commission. Most states have created their own regulatory agencies and regulations that must be obeyed by organizations operating in those states, and state regulations can be different, and sometimes more restrictive, than the federal regulations. N o attempt will be made here to provide details on the current regulations on waste and concentrations in effluent streams, and there is no way to know how those regulations will change in the near future. However, the reader should read the regulations or explanations of the regulations. One likely change in these acts in the near future appears to include giving more consideration to the “risk’ of a contaminant. Such a change appears to be particularly interesting to Congress. Under risk analyses, the release limits could become different for different forms of a contaminant and even different under different local conditions that would affect the likelihood of the contaminant reaching the public or sensitive parts of the environment. Costs of remediation or release reduction could also become a factor in setting acceptable release rates and concentrations. That is, cost-benefits may become important to the regulations. (The “benefit” part of the analyses is likely to benefit society, not necessarily a particular company) Although the allowed levels of contaminant release are almost certain to remain sufficiently low to present no more than accepted risk, there is a growing recognition that it is not possible to always achieve zero release or zero risk of release. Under these real conditions, there is a practical level of effort that should be expended to “minimize” release or to bring the releases to lower and lower levels. It may be more effective

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to use the remaining funds to reduce further the emission of other pollutants that may be posing more risk. Risk analysis, if used properly, can

suggest the most appropriate way to expend our efforts and resources to reduce dangers to human health and the environment. Risk analysis can, in principle, determine when it is more appropriate to start expending more effort on other problems rather than trying to reduce an individual emission much further. Such risk-based regulations could make it possible for some facilities to release more of some contaminants, but there is no assurance that such analyses will not make the release of other contaminants even more restrictive. The merits of risk-based regulations are the opportunites to base all release regulations on comparable bases. Perhaps the greatest potential benefit from expanded use of risk analysis could be the increased focus of regulations and waste and environmental treatment efforts on the most important problems, problems that were not necessarily obvious from less rigorous approaches. Risk analysis will have to be at least somewhat specific to the site, and requirements for risk analysis are likely to complicate the selection of waste treatment methods for some contaminated sites. The availability of reliable risk analysis methods will be critical to the success of any such changes in regulations. Risk analyses always predict a probability of damage to the public or the environment, but it is also important to know how accurate and reliable those probabilities are. If more reliance is to be placed on risk analyses, we will certainly need reliable methods and information to make the risk assessments; otherwise, there could be an increase in “risk’ by greater use of risk analyses. Of course, the present regulatory system is ultimately based upon a concept of risk, but the regulators have approached the problem in a more generic way to set release restrictions that will apply to all sites, and the pathways through which contaminants endanger human health or the environment appear to be the most conservative available. Regulations appear to have been developed by separate individual studies that do not necessarily use the same assumptions and techniques. It is also not clear that political considerations (usually through the level of public concern) do not sometimes override scientific evaluations of the problems. The proper use of risk analyses could put environmental regulations on a more rational basis and could provide better regulation by highlighting problems with specific sites and at reduced cost, if it is possible to reduce the restrictions on some sites. On the other hand, risk-based regulations are likely to restrict releases of contaminants at certain sites that are particularly sensitive because of large local populations, endangered specie, or unfavorable geology. The restrictions at those sites could become significantly more difficultto meet than the current regulations. Of course, if

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CHAPTER 1

the regulations are based upon valid risk analyses, such restrictions would be justified. There is also some consideration in Congress to change the liability basis for environmental cleanup. Although there is no way to be sure what changes, if any, will result, the complaints with current regulations appear to focus on the practice of holding each contributor to a contaminated site potentially liable for the entire cleanup effort and cost, regardless of the amount of material they added to the site or the toxicity of the material they added. This clause is viewed as grossly unfair to many, but any changes in regulations to limit any organizations responsibilities to the portion of the contamination they contributed will certainly leave some difficult questions to answer. How does one determine how much each organization is responsible? Who is responsible for the contamination for which no source is identified. There are also questions of who will pay for cleanup of contamination created by organizations that no longer exist or that cannot possibly (with their total assets) pay their share of the cleanup. Resource Conservation and Recovery Act

The Resource Conservation and Recovery Act (RCRA) is usually the principal regulation for solid wastes. Although the act is intended to encourage conservation and recovery of resources and does do that, its regulation of the storage and disposal of solid wastes is often the major reason for its importance. “Hazardous” wastes fall into one or more of four categories based upon their ignitability, corrosiveness, reactivity, or toxicity. The RCRA regulates both the disposal and storage of hazardous wastes. Its objectives include prevention of long-term on-site storage that could eventually result in a legacy of wastes stored at abandoned industrial or waste storage sites. Waste must be treated properly and removed to approved storage facilities or disposal facilities in a timely manner. The RCRA classifies wastes as hazardous if they come from certain sources (listed wastes) of if they have certain characteristics (wastes that are hazardous by characteristics). A waste can be hazardous in any of several ways. Ignitable wastes are liquids with a flash point lower than 60°C (as determined by the Pensky-Martens closed-cup test or an approved equivalent test), gases that can be ignited, wastes that are strong oxidizers, and solid wastes that are capable of starting a fire through friction or from spontaneous chemical changes at standard temperature and pressure. Corrosive wastes are usually liquids. They can have a pH less than 2 or greater than 12.5. To be noncorrosive, the liquid must also not corrode

/NTRODUCTlON

9

steel (SAE 1020) at a rate greater than 6.35 mm/yr at a temperature of 55°C. Reactive wastes are those that are unstable enough to undergo violent changes (even without detonation), react violently with water or release toxic gases upon reaction with water, or capable of detonation from an initializing force. Toxic wastes are those that can be leached in the environment and release toxic components in concentrations greater than specified limits. Environmental leaching is simulated by a standard leach test specified in Appendix I1 of 40CFR261 or by an equivalent and approved method. The allowable concentration limits in the leach liquor from the standard test are given in Table 1 of 40CFR261.24. The concentrations allowed in the leach liquor are usually tied to the drinking water standards associated with the Clean Water Act (Table 1). The toxicity standards appear to be the most important aspects of most solid wastes, and this book will focus somewhat on the toxic materials in liquid and solid waste streams. In the RCRA, the EPA also defined certain wastes as hazardous simply because of their source and/or the presence of certain components. These are called “listed” wastes because there is a “list” of such wastes. This is explained in Appendix VIII of 40CFR261. There are four “lists” of hazardous waste, each designated by an F, K, U, or I? List F includes hazardous waste from nonspecific sources but with specific hazardous components. List K includes wastes from specific sources. See 40CFR261.32. Lists P and U include discarded products, off-specification products, and spilled or stored residue from these sources. List P includes the most acutely hazardous wastes, and list U includes the others. Table 1 gives some of the wastes that fall into each of these lists. Details of the listed wastes are given in the regulations (40CFR261.32). If a waste is not included in any of these lists, it can be nonhazardous or hazardous by characteristics. If a waste is not ‘‘listed,’’it can be still be hazardous if it fails one or more of the criteria given earlier for defining hazardous wastes (hazardous waste “characteristics”). For instance, the waste could fail the standard environmental leach test. If a waste is listed, it is declared hazardous regardless of its characteristics or performance in any of the specified tests. There is often confusion and doubt about the wisdom of declaring wastes toxic even if they do not show characteristics of hazardous wastes (although most listed wastes probably will show such characteristics). Although the intent of all aspects of regulations is not necessarily obvious, it is likely that the use of listed wastes is intended to place the burden of proof that a waste is not hazardous on the generator of the waste and to prevent the use of dilution as a tool to make a toxic waste nontoxic.

10

CHAPTER 1

TABLE1 RCRA “Listed” Wastes F-Serfes:Hazardous wastes from nonspecific sources, except those excluded by other regulations such as 40CFR260.20 or 260.22) Spent selected halogenated solvents and solvents used in degreasing that contained initially 10%or more by volume of halogenated components Pol) Other halogenated solvents that contain 10%or more by volume of the halogenated solvents and still bottoms from the recovery of those solvents (F002) Solvent waste that contain before use 10%or more of selected nonhalogenated solvents such as xylene, acetone, ethyl benzene, MIBK, ethyl acetate, ethyl ether, etc. (F003) Solvents and residue that contain before use 10%or more of selected solvents such as cresols, cresylic acid, or nitrobenzene before use (F004) Solvents and residue that contain before use more than 10%of selected solvents such as benzene, toluene, methyl ethyl ketone, carbon disulfide, isobutanol, or pyridine (F005) Wastewater treatment sludges from electroplating operations, except for selected plating operations such as tin plating, anodizing of aluminum, zinc plating, aluminum plating, and some cleaninglstripping operations associated with plating these materials (F006) Spent cyanide plating bath solutions (F007) Residues from the bottom of plating baths (FOOS) Spent strippingkleaning bath solutions from processes where cyanide is used (F009) Residues from oil-quenching baths from metal treating where cyanides were used (F010) Spent cyanide solutions from salt bath cleaning from heat treatment of metals (F011) Wastewater from quenching after heat treatment of metals where cyanide was used (F012) Wastewater treatment sludges from chemical conversion coating of aluminum (FO19) Wastes (except for wastewater and spent carbon from HCI purification) of vi- or tetrachlorophenol used in the production of pesticides or their derivatives (F020) Wastes (except for wastewater and spent carbon from HCI purification) from production of pentachlorophenol or intermediates (F021) Wastes (except for wastewater and spent carbon from HCI purification) from production of tetra-, penta-, or hexachlorobenzenes under alkaline conditions (F022) Wastes (except for wastewater and spent carbon from HCl purification) from production of tri- or tetraphenols (F023) (continued)

11

TABLE1 (Continued) Wastes from processes using free-radical-catalyzed processes such as the production of chlorinated aliphatic hydrocarbons (F024) Wastes (except for wastewater and spent carbon from HCI purification) that were produced in equipment used previously in the production of tetra-, penta-, or hexachlorobenzene under alkaline conditions (F026) Discarded formulations using tri-, tetra-, or pentaphenols or materials derived from these compounds (F027) Residues from the incineration or thermal treatment of soil contaminated by hazardous wastes of the type F020, F021, F022, F023, F026, or F 0 2 7 K-Series: Solid wastes from specific sources Sediments from treatment of wastewaters from wood-preserving processes that use creosote and/or pentachlorophenol (KOOl) Wastewaters from production of any of several inorganic pigments (KO02 through K008) Distillation and stripper bottoms from the production of several hydrocarbons and halogenated compounds (KO09 through K020, KO22 through K027, K029, K030, K083, K085, K103, and K136) Certain spent aqueous and solid catalysts (KO21 and K028) Certain wastewaters, condensate, and adsorbents ( K l l l through K118) Brines and inorganic sludges (K071, K073, and K106) Various wastes from the production of pesticides (KO31 through K042, K 9 7 through K99, and K 1 2 3 through K126) Wastes from the manufacture of explosives (KO44 through K047) Sludges, floated material and emulsions, and heat-exchange cleaning residue from petroleum refining (KO48 through K052) Furnace exhaust dust and pickle liquor from the steel industry (KO61 and K062) Dust or leach liquor from lead treatment (KO69 and K100) Wastes from the production of veterinary pharmaceuticals (K084, K101, and K102) Wastes from ink production (K086) Ammonia still lime sludge and decanter tank tar sludge from coking operations (KO60 and K067) P-Series: Discarded commercial chemicals, container residues, spill residue, and off-specification chemical products More than 100 chemicals are listed by the EPA, including organic and inorganic compounds. U-Series:Commercial chemical products, off-specification products, and chemical intermediates A long list of chemicals and intermediates is given by the EPS,most of which are organic.

12

CHAPTER 1

The EPA provides a procedure for “delisting” a listed waste [ 4 ] . Delisting i s not a simple procedure and is only worth attempting when large volumes of waste are involved. Delisting, of course, involves showing that the waste does not fail any of the tests for hazardous wastes. Because the waste has been considered hazardous initially, delisting requires proof that the waste does not fail any test and that the waste used in the tests is truly representative of the waste being delisted. One certainly should seek delisting of any waste that is truly not hazardous, but one should not expect the delisting to be a quick procedure. Drinking Water Standards Drinking water standards were issued under the Safe Drinking Water Act (40CFR141) and are important to waste and environmental treatment

TABLE2 National Primary Drinking Water Standards

Compound Arsenic Barium Cadmium Chromium Fluoride Lead Mercury

Nitrate (as nitrogen) Selenium Silver Endrin Lindane Methoxychlor Toxaphe ne 1 , 4 - (2,4-Dichlorophenoxyacetic ~ acid) 2,4,5-Tp (Silvex or 2,4,5-trichlorophenoxypropionicacid) Radium Gross alpha radioactivity Thrbidity Coliform bacteria

Allowable concentration (mg/L) 0.05 1.0 0.01 0.05 4.0 0.05 0.002 10.0 0.01 0.05 0.0002 0.004 0.1 0.005 0.1 0.01 5 pcm 15 pCi/L l/turbidity unit 1/100 mL

13

/NTROOVCTlON

problems because they affect the concentrations that need to be reached by treatment of water effluents and groundwater and because the concentrations of toxic materials in the standard environmental leach test approved for the RCRA are tied to the drinking water standards. Mowable concentrations in discharge waters will not always be required to be as low as the drinking water standard because of subsequent degradation or dilution of contaminants before it is reasonable for anyone to drink the water, but the allowable release concentrations are still likely to be affected by the drinking water standards. There are even a few cases where it may be necessary to reduce contaminant concentrations to levels below the drinking water standards, such as when surface discharge of the water would be more harmful to fish than to humans. In those cases, one can think that the discharge standards will be set by standards other than the drinking water standards. The drinking water standards are subject to change as more materials are found to be toxic, but the National Primary Drinking Water Standards are shown in Table 2. This list tends to include some of the more common acute toxic materials. There is also a Secondary Drinking Water Standard shown in Table 3 (see 40CFR143.3). Note that the secondary standards include less specific materials, such as those that cause color or odor, total dissolved solids, corrosiveness, and all foaming agents. Several materials are included that are common in most waters, but whose concentration should still be limited.

TABLE 3 National Secondary Drinking Water Standards Material Chloride Color Copper Fluoride Foaming agents Iron

Manganese Sulfate Zinc Total dissolved solids Color Corrosiveness Odor

PH

Allowable concentration (mg/L)

250 15 color units 1

2 0.5

0.3 0.05 250 5 500 15 color units noncorrosive 3 x threshold odor number 6.5-8.5

14

CHAPTER 1

NEW TECHNOLOGIES FOR WASTE AND ENVIRONMENTAL TREATMENT In addition to growing in size and financial importance, the waste and environmental industries are still growing in scientific and technical ways. Considerable research and development efforts are devoted to waste and environmental treatment, to find new treatment methods and change the way the industry works. Greater use of separation methods is likely to occur as new technologies are developed to handle specific wastes and waste streams, and these new technologies may include significant innovations. There is some concern that the research and development in the industry are geared too closely to testing and demonstration and are not encouraging participation from companies that are most proficient in developing high technologies. On the other hand, there is also concern that many “high-tech” approaches will prove too costly for many applications, especially those that involve large volumes of soil and groundwater. This particular concern may be relevant to only some types of “high-tech” concepts, not to all concepts offered by large and/or advanced companies. In some ways, the current approaches to environmental regulation have not encouraged development of new and innovative regulations. Regulations that require extensive validation before a technology can be accepted can also slow the development and application of new technologies; such requirements can be justified or not justified. Any regulation that slows the deployment of new technologies is likely to slow the growing importance of new separation methods. Essentially all industrial companies want to meet all environmental regulations and even to protect the environment and the health of their workers and neighbors. However, there is room to debate how much effort and, most importantly to businesses, how much money should be expended for these purposes. There is even a degree of fear in some industrial communities that as new technologies are developed they may be forced to spend considerable funds to install the technologies at their facilities even if the technologies at their facilities are, in their opinion, adequate. This fear comes from the requirements to use the “best available technologies.” Although there are merits in installing new technologies, no company is pleased to find its newly installed “best available technology” no longer the “best” and must be replaced. This concept of requiring the best technology is reasonable in a static industry, but because new waste and environmental technologies are constantly being developed, it can become impractical to replace its effluent control equipment too often if better technologies are developed rapidly, especially if the improvements are relatively small. The merits of

/NTRODUCTION

15

installing new emission technologies depend upon the current environmental and health effects from the current technology and the degree of improvement that would result from installation of the new technology. It is possible that there will be little incentive for the user of the technology to develop improved waste treatment methods for existing facilities as long as the currently installed technology is viewed as adequate; the principal incentives to develop better technologies may lie with the government and equipment suppliers who would benefit from selling the new technology. Most companies will be more likely to consider the very best technologies for new facilities than for replacing equipment at older facilities. Even if it is somewhat more costly to install a newer technology, improved performance may reduce the likelihood that the company would have to make changes soon to meet new regulations. There are several notable cases where companies found that they could reduce emissions by recovering and reusing components. They sometimes actually reduced costs, and the changes were profitable as well as environmentally desirable. These cost reductions probably incorporate the cost of waste disposal that has risen so steeply during the past decade. However, companies may be less interested in installing better technologies to replace equipment that they and the regulators once (or even recently) viewed as adequate. The difficulties in “proving” that a new technology is superior can also be a deterrent to development and application of better technologies. This problem is not unique with the waste and environmental industries; every technology developer must convince the customers that they have developed a truly improved product. The special difficulty for the waste and environmental industry is the need to convince both the customer companies and the regulatory agencies that a new technology is significantly better. The motives of these two groups can be different. It may not be difficult to convince regulators that a new technology with costs comparable to or greater than the existing technology is better and worth using, but it may be more difficult to convince the companies. On the other hand, it may be easy to convince the companies that a new technology that is less costly but gives comparable performance is an improvement, but regulators may be more skeptical. According to some the regulatory agencies, and especially the EPA, stress enforcement of the laws over protection of the environment. They contend that it may be better to work more closely with some industrial groups such as those developing waste and environmental technologies. That would help bring new technologies into regulatory approval and thus speed the rate at which better technologies for treating waste and contaminated environment are implemented. However, that would also

16

CHAPTER 1

create the possibility for the agency to become a “captive” of industries. Then the public and the environment could suffer. Critics of closer association of the EPA with industry cite other regulatory bodies that play important roles in promoting the industry they regulate. There is a fundamental difference between the EPA and most other industrial regulatory agencies that could make it less likely that the agency would become captive to industries. Most other regulatory agencies are responsible for single industries or groups of industries. In those cases, it may be in the interest of the agency personnel to have the industries they regulate flourish. Complete decline of the industry would eliminate the need for the agency, and thus the need for the regulators. The EPA, however, is responsible for essentially all industries as well as governmental agencies, individuals, and others who d o or could pollute the environment. It may be easier for the EPA to remain independent of each individual industry while taking a more active role in helping the industries develop and test better environmental treatment methods. Although the EPA does play important roles in technology development and testing, its focus does appear to be much stronger on the enforcement part of its mission. Of course, enforcement of good regulations does protect the environment, but the agency also serves the public interests when it properly helps industries to improve their protection of the environment through innovation and apply enforcement activities only when other approaches fail. It would be difficult to prove that the EPA and other regulatory agencies are approaching their tasks in the wrong way, but the reports that companies involved in programs such as the Superfund projects are spending more on legal activities than on solving the problems d o suggest that something is preventing the most efficient use of the funds from either the government or industry for waste and environmental cleanup. However, such reports do not clearly show whose policies are at fault, and one should not quickly blame the EPA or some other government agency. There may be tendencies for companies to defend their position legally rather than solving the problems, It is difficult to determine if such practices actually save money in the long term. This could be just another example of the apparent trend in the United States to go to court first and to think or evaluate later. The personnel decisions of regulatory agencies are also criticized by some who claim that regulatory agencies have too many legal staff and too few scientists and engineers who could analyze new technologies reliably and confidently approve new technologies. Again this criticism reflects different judgments of the regulators’ roles of enforcement and assisting in improving environmental quality. Since most readers of this book are

/NTRODUCTION

17

likely to be engineers or scientists, even the readers may hold some bias on this issue. Nevertheless, the need for new and improved approaches to the treatment of wastes and environmental problems is so clear that new technologies are essentially certain to be sought and adopted. Otherwise, the cost of waste and environmental treatment will continue to rise at a rate greater than the gross national product and will become an increasing economic burden unless we become willing to accept less control and greater environmental hazards. New separation technologies will play major roles in the use of new technologies. ORGANIZATION OF THIS BOOK There are two major parts of the book. The larger part covers chemical separation methods, such as adsorption, gas absorption (and stripping), liquid-liquid extraction, membrane processes, etc. The second part covers physical separation methods, such as filtration and sedimentation. The chemical methods separate materials as individual molecules, while physical methods separate large groups of molecules such as solid particles or liquid droplets, Although the careful reader will discover that there is no clear distinction between several of the separation methods, and not even a clear distinction between some chemical and physical separations when macromolecules are involved, the topics will be covered in chapters that are most appropriate. Although the molecular separation methods believed to be of most importance to environmental and waste applications are covered by complete chapters, a few other separation methods could have some applications and do deserve some mention. These methods are grouped with related separation methods into a separate chapter with other separation methods that are likely to have more limited applications in waste and environmental processing. In these cases, much less detail is given. In most cases, there will be no quantitative description of design methods for the separation methods that are covered only briefly, but the similarities to design methods for other separation methods are mentioned. The aim of these descriptions is to give the reader an understanding of how the method works and for what problems the method could be considered, not to prepare the reader to design systems using these less common methods. Even in these short descriptions of the less common separation methods, there is an effort to describe the limitations of those methods, especially the limitations for their use in waste and environmental processing. In some cases, the limitation on the method may be

18

CHAPTER 1

the inability of the method to compete economically with other methods at the moderate-to-high throughput usually required for most waste and environmental processes. Several separation methods are available that are effective, but are currently far too costly to use o n high-throughput systems, such as many industrial effluent systems. However, with further development and larger-scale deployment, the costs for some of these methods may decline sufficiently that larger-scale applications to waste and environmental problems become practical. The second part of the book is devoted to physical separations, i.e., separations of different phases. They could be separation of solid particles from gases or liquids, separation of different liquid phase, or separation of different solid phases. The best way to divide the separation methods between molecular and physical separations is not always completely obvious, and examples are pointed out where there can be difficulty in deciding whether a separation is molecular or physical. In those cases, the rationale for placing the separation method in one group or the other is described, but other authors may choose to divide the topics differently The largest part of the physical separations part of the book is devoted to filtration methods. Filtration is so common in most process industries, including waste and environmental processing, that it deserves first billing in this part of the book.There are two sections in the chapter on filtration. The first is devoted to “surface” filters, i.e., filters in which the filtration takes place largely outside the filter medium. The principal filtration occurs at the surface of the filter medium or in a filter cake that builds up on the filter medium. These are also sometimes called “cake filters” because the filtered particles accumulate on the filter surface and form a “cake.” This is probably the most common form of filtration and certainly the most easily recognized to most people. The second filtration section is devoted to “deep-bed” filters. Those are filters in which the particles are removed largely within the filter medium, usually within a bed of fibers or granules. There are many differences in filters covered in both of these sections; so each chapter is further divided to describe some of the variations in each broad class of filters. The design methods or considerations for each class of filter are different, but the design considerations for different variations of filters within each class are usually similar, and many of the design procedures will be the same or similar for all filters within each class. As with the molecular separation chapters, a few general considerations are given on conditions under which each class and variation of filter is most likely to be favored. Within each part of the book, chapters cover the separation methods most common or most important for waste and environmental problems. The amount of detail provided in each chapter comes from the current

kTRODUCTlON

79

and/or expected importance of the method to waste and environmental problems. The relative importance of the separation methods in waste and environmental problems is not expected to be the same as their importance in the current process industries, so the reader often will find methods covered in either more or less detail than is usually given in books of similar length that do not focus on waste and environmental problems. Of course, to distribute the pages in the book among the different separations methods, it was also necessary to predict which methods will grow in importance so they can be covered in more detail.

CONTENT OF THE CHAPTERS Each major chapter describes a particular separation method, the “science” or basis for the separations, some of the more common types of equipment used for this separation method, the principles used in “process’’design of the equipment (generally sizing of equipment and estimation of the performance of equipment), examples where the method can be used in waste and environmental problems, and a general discussion of the competing separation methods and the conditions under which this method is more likely to be the most practical. Each major chapter begins with a general description of the separation method and a few waste or environmental applications. This early mention of one or more applications is intended to give the reader an immediate idea of the potential benefits of the method. This is followed by a brief description of the types of equipment that can be used and a description of design methods. Then the reader is better equipped to understand the conditions under which the method i s most likely to be the preferred one to use. The chapters then usually close with mention of a variety of applications of the method to waste and environmental problems. The list of applications is not complete (and would not be likely to remain complete if it were), but it is intended to give the reader a chance to think of the conditions under which the method could be used. The list and description include applications in active use and potential applications that have been studied. Each chapter also includes a description of the most likely competing separation methods and the conditions under which the method being studied is believed to most likely be practical.

LEVEL OF DIFFICULTY AND USE OF THE BOOK The reader is expected to be a graduate or an upper-level undergraduate in engineering or one of the physical sciences. Chemical engineers

20

CHAPTER 1

and chemists are likely to find the book easier reading. However, in many ways the book may be of more use to environmental engineers and others working on waste or environmental projects who have had less background in separation methods. It is important that the reader have some basic knowledge of chemistry, but no advanced chemistry is needed. An introductory course, such as freshman chemistry, will be adequate for most of the book, but there will be advantages in have a somewhat stronger chemistry background. Those with very strong chemistry backgrounds may find some of the discussions oversimplified, but that is a risk that must be taken if the book is to have a sufficiently wide appeal. The mathematics involved should not challenge those with engineering or physical science backgrounds. Generally, the standard undergraduate calculus background will be fully adequate; in most cases, basic algebra will be adequate. There are references to more advance mathematical methods, but it is usually not necessary to understand the more complicated details to use the results. Readers are expected to have an interest in waste and environmental problems, and often may have the responsibility to select or design separation treatment methods for the problems. It will be best if the book can be first studied as a whole since that is the only way to develop a basis for comparing separation methods and making selections. However, each chapter can be used as a reference book where the reader can study selectively those methods in which he or she is interested. Most chapters discuss competing methods when they are most likely to be serious competition to the method being discussed. Then readers can decide if they need to study more than one chapter for a given problem. It is anticipated that most readers would first read the book and then use it as reference material and review chapters pertaining to separation methods that may be of importance to the problems of concern at the moment. These cross references to competing methods may be one reason for using the book as a reference source. Many environmental engineers and others working on a variety of waste and environmental issues may find it difficult to remain expert in all of the separation methods of potential use and will want to refer to the appropriate chapters occasionally. The level of detail is considered appropriate for an overview, a review, or a “brushup” on selected separation methods. The chapters are short enough to be reviewed relatively quickly The design procedures are given for several reasons. First, they provide insight into what is important to the size, cost, and performance of equipment. This insight is needed by those who select separation methods and by those who purchase equipment that others design. Some familiarity with the procedures is needed just to evaluate the work of

/NTRODUCTION

21

others who may actually be designing and/or supplying the equipment. In many chapters, the description of design procedures is adequate for actual design of equipment. The reader designing separation equipment is encouraged to use computer procedures when available, but they are also encouraged to understand the procedures before relying upon the computer packages. Such understanding can be important in evaluating results of calculations and seeking alternative parameters, perhaps even other design specifications. Even when equipment is supplied by outside vendors, the buyer needs to understand how it works. Those involved in research and development, consulting, or technical sales for a variety of separation methods may want to use the book in a similar manner, but those involved only in specific separation methods are likely to find that the chapters on those particular methods do not contain sufficient detail. Those people will need to be familiar with some of the most detailed specialty tests devoted to single separation methods or even specific aspects of those methods. Those involved on the leading edge of research and development need to remain aware of even the latest developments and should remain familiar with current journals and reports as well as current specialty books; no book can be or remain adequate to meet all of their needs. Such current information seldom can be obtained by books alone. However, even those actively involved in developing advances in individual separation methods may find the coverage of the other sections helpful to explore and evaluate alternatives to their methods. In developing any new technology, it is certainly useful to understand the competition as well as to know what standards the technology must reach.

REFERENCES 1. Pollution Prevention Act of 1990. 42 U.S.C. section 13101-13109 (1990). 2 . Browner, C.M. EPAJ., 1 9 , 6 (1993). 3. Anastas, l? T. and T. C. Williamson (Eds.). Green Chemistry: Designing Chernistryfor the Environment. ACS Symposium Series 626, Washington, DC (1996). 4 . US.EPA, Petitions to Delist Hazardous Wastes-A Guidance Manual, EPN530SW-003 (1985).

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Adsorption and Ion Exchange Adsorption is the removal of a component from a fluid by physical or chemical attachment to a solid. Ion exchange is the substitution of one ion in or on a solid for an electrically equivalent number of ions from a solution. Although adsorption and ion exchange are different chemically they are treated together in this volume because their operations are similar in so many ways. They both usually involve pumping a fluid through a bed or column packed with solid adsorbent or ion exchange materials. They are both important operations for removing toxic materials from liquid or gaseous wastes, especially for those components at low concentrations. Adsorption and ion exchange are becoming so important in waste and environmental processing that they are treated with considerably more detail in this book than in most other books on general separation topics, but, of course, even more details can be found in books dedicated entirely or primarily to adsorption operations. This importance of adsorption in these applications results largely from the ability of adsorption processes to remove components from very dilute fluids (gas or liquid) economically, and the importance results partially from the ability of adsorption beds to incorporate large numbers of separation stages (or transfer units) into modest size equipment. Adsorption can also be important in the removal of valuable materials from waste fluids. Even in cases where other methods are more economical for removing the bulk of the component(s), adsorption or ion exchange may be the best choice for a “polishing” step to remove the last traces of the component(s). Adsorption and ion exchange are particularly attractive for removing dilute components, a common problem in pollution control. Usually the adsorbed material, toxic or valuable, is recovered in a concentrated form for disposal or reuse. The solid adsorbent can often be regenerated for reuse, and the adsorbed or exchanged component(s) can be recovered in a concentrated form. When the toxic component(s) can be recovered 23

24

CHAPTER 2

alone or in a concentrated form, waste disposal costs are reduced because the volume of waste sent to disposal is reduced. The merits of adsorption depend upon its ability to reduce the concentration of the toxic components in effluent streams (often air or water) manyfold, sufficiently to permit release of the fluid, and upon its ability to concentrate the toxic materials sufficiently that disposal, destruction, or subsequent use of the materials will be less costly Current regulations generally give little financial incentive for removal of toxic components from waste streams unless the concentration is reduced sufficiently that the fluid can be released or that entirely different disposal methods can be used. This means that the concentration of the toxic component must be reduced below some specified value. Because adsorption and ion exchange are usually most effective with dilute solutions (liquid or gas) and can reduce concentrations many-fold, they are attractive for use as “polishing” steps to reduce the concentrations of contaminants to acceptable levels, perhaps after another approach has removed the bulk of the contaminant. Adsorption also can be used to fix toxic materials in forms that are not hazardous simply because they are not easily removed from the solid. In those cases, the adsorbent may be part of a “waste form,” and the adsorbent and toxic materials may be sent to disposal together. It still may be necessary to incorporate the adsorbent into an additional waste form such as concrete grout, but the adsorbent can help hold the contaminant in the waste form and thus meet EPA leaching restrictions. If the toxic material is combustible, it could be removed from the adsorbent and destroyed by incineration. The adsorbent could also be burned, or the adsorbent could be regenerated by burning off or otherwise destroying the contaminant. (Note that there is considerable public concern with incineration and often severe limitations on its use.) The adsorbent loaded with toxic contaminants could be sent to a landfill without further treatment if leaching of the toxic materials is sufficiently slow or if the landfill is protected to recover and prevent release of leached toxic materials. Otherwise, as noted, the adsorbent could be incorporated into a grout or another solid form with zero or extremely slow release rates, rates that pass EPA leach tests.

ADSORPTION EQUIPMENT Adsorption operations usually involve passing the fluid over a static fixed bed of “adsorbent” particles until the bed is sufficiently loaded that the sorbate (solute or contaminant) can no longer be removed effectively

ADSORPTION AND /ON

EXCHANGE

25

fluid in

fluid in FIGURE 1 Adsorption bed showing the transient nature of a typical adsorption operation. Adsorbate accumulates in the bed with time.

(Figure 1).This transient type of procedure is only one way to operate an adsorption separation, but it is by far the most common procedure for bulk (high volume) processing operations such as those that are important in waste treatment. The feed stream is fed constantly to the adsorption bed, and the treated fluid exits the other end of the bed with a greatly reduced concentration of the adsorbed solute. There is thus an accumulation of the solute in the bed. The solute is adsorbed initially near the top (inlet) of the bed, and solute moves down the bed as the concentration on the adsorbent accumulates and approaches the concentration that is in equilibrium with the feed stream (Figure 2). Figure 2 shows the idealized accumulation for a “favorable” (to be defined later) adsorption. The upper diagram shows the accumulation in the bed at different positions for three times after adsorption begins. The diagram shows the concentration in the fluid, but this concentration (as will be seen) is approximately proportional to the loading of solute on the adsorbent. Similarly, after time 2, the front will have moved farther down the bed. The lower diagram

CHAPTER 2

26

z, position in the bed

t

FIGURE 2 Movement of concentration fronts down an adsorption or ion exchange bed: (a) Concentration profile within the bed after different times; t l < t g < t 3 . (b) Appearance of an adsorption front plotted as concentration seen as a function of time at fixed positions in the bed; z1 < z2 < z3. shows the concentration in the fluid exiting the bed as a function of time. Note that there is no solute in the fluid until breakthrough occurs. Then the concentration rises to the feed concentration. This is the type of operation covered most extensively in this book. In more realistic cases, the leading edge of the front in the bed and the breakthrough curve exiting the bed look like S-shaped curves rather than vertical steps. Since adsorption operations usually are not steady-state operations, the adsorbent bed must be replaced or regenerated after it is used (sufficiently loaded). Steady-state operations with some solid adsorbents have been proposed and used, but they are not common and will be mentioned only briefly. When lower removal efficiencies can be tolerated or

ADSORPTION AND ION

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27

when the adsorbent has a particularly strong affinity for the toxic adsorbate, fluidized beds of adsorbent or even stirred tanks can be used, and the adsorbent can be removed and added continuously. These types of operations are generally limited to relatively low removal efficiencies because mixing (and fluid bypassing) allows some toxic materials to escape the adsorbent. One additional important merit of fluidized adsorption beds is their ability to handle small but significant quantities of solids in the feed; packed beds can tolerate only very small quantities of solids in the feed. Stirred tanks of ion exchange resins have been used to recover minerals from slurries of leached ores, where there are especially high concentration of solids in the feed. The limited number of separation stages in fluidized or stirred beds of adsorbent or ion exchange material results from the mixing of both the fluid and the particles in a fluidized bed; this can severely limit the performance of some systems. However, one can increase the performance of fluidized beds in several ways. The fluidized bed volume can be divided into several smaller fluidized beds operating in series. In such cases, it may be possible to make each smaller bed perform approximately as a stage. A similar effect can be achieved by using adsorbent particles with two sizes. If the sizes of the particles differ sufficiently, the fluidized bed will separate the adsorbent particles with the smaller particles above the larger particles [ 11. This makes the bed function approximately like two beds in series. It is also possible to add magnetic particles to the bed and to apply a magnetic field after the bed is fluidized. The magnetic field restricts or prevents motion of the magnetic particles and thus holds the other (adsorbent) particles in approximately stationary positions in the bed [2]. This can make the bed function somewhat like a “fixed bed” but with the bed expanded sufficiently by the fluidization to allow a lower pressure drop.

Continuous Operations Other approaches to continuous adsorption or ion exchange involve continual or incremental movement of a packed bed of adsorbent or of an adsorbent fabricated in a different form such as a continuous belt, a disk, or a wheel. Such operations have found practical uses, but they are far less common than the simpler packed beds. Other “continuous countercurrent” systems have physically moved the adsorbent or ion exchange material. The solids can move as fixed beds as in the Higgins column, which has been used for continuous ion exchange processes, or can move as a series of fluidized beds which flow from one part of the system to another. Keller recently reviewed adsorption and ion exchange equipment [3]. In other continuous methods, the adsorbent is constructed as a porous monolith

28

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rather than as a bed of random spaced adsorbent particles, and the monolith can be moved mechanically in the direction countercurrent to the fluid. The porous monolith can be constructed as a “wheel” of adsorbent. Similar mechanical movement of solid adsorbents also can be achieved by transport of baskets or other porous particle containers countercurrent to the fluid. “Simulated’ steady-state operations can be approximated by using several transient packed beds by periodically changing valving so the feed, elution, and product enterAeave different beds sequentially [ 4 ] . However, the following discussion will deal largely with the more common “fixed” bed operations which are far more likely to be used in waste and environmental treatment. There are the dominant systems in industry overall, and they are expected to remain so for a considerable time.

Elution Chromatography Elution chromatography is a different way to operate an adsorption process. An adsorptiodelution chromatographic method commonly used in analytical separations first involves placing a small sample of material to be separated in the upper portion of the column and then flushing (eluting) it down the bed. The different components of the sample are eluted down the bed at different rates and can be detected sequentially as they are eluted from the bed. Since elution chromatography is not commonly used in bulk waste treatment, it will not be discussed extensively More details on elution chromatographic separations are usually found in textbooks on analytical chemistry. Gas chromatography is a form of elution chromatography that has become a standard method for analyzing multicomponent gas mixtures. Liquid chromatography is of growing importance in analyzing multiple solutes in liquid streams, especially solutions of biotech materials. Elution chromatography is usually used to separate small quantities of materials, and it is usually limited to analytical chemistry and the separations of quite valuable materials such as those from biotech operations. Elution chromatography is a relatively slow operation that is not suitable for high volume and/or low value materials. In waste and environnrental operations, elution chromatography is more likely to be used as an analytical chemistry tool than for bulk chemical separations.

TYPES OF ADSORBENTS Materials used as adsorbents can be categorized in several ways. The adsorbents can be natural materials, usually with irregular granular shapes,

ADSORPTION AND

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29

or specially manufactured materials, in granular or specifically selected shapes. Even this simple categorization has problems because the “natural” materials can undergo various degrees of treatment before reaching their most effective form as adsorbents. Alternatively, adsorbents could be classified as organic materials or inorganic materials, as hydrophilic materials or hydrophobic materials, or in many other ways. Perhaps the most common adsorbent materials are activated carbons, treated natural adsorbents. This is a high surface area carbon product usually prepared by charring a cellulose-based starting material. One of the oldest and most interesting applications of charcoal is in the removal of undesirable compounds from whiskeys and related alcoholic drinks. Scotch whiskey and U.S. bourbons are “aged” in partially charred barrels so undesirable compounds can be adsorbed by the charcoal on the sides of the barrel. Of course, other reactions also take place during the aging process, but the adsorption contributes to the desirable taste of the final product. The carbon can also be used in more conventional packed beds. One well-known domestic producer advertises its “trickle bed” adsorber used in manufacture of its “sipping whiskey.” Other untreated natural materials such as coal, wood, and various minerals are also used as adsorbents. The most effective adsorbent materials are usually high surface area materials with either specific pore or cavity sizes or with specific active surfaces. Numerous manufactured materials are used as adsorbents. Adsorbent materials produced in large volumes include silica gels, synthetic zeolites, and forms of cellulose. Note that cellulose-based adsorbents could be regarded as natural or manufactured, depending upon the amount of processing required. Many very effective, but relatively costly, adsorbent materials are entering the market for high value applications, principally for chemical analyses by elution chromatography. The financial opportunities in producing high quality adsorbents are high. Adsorbents are also often categorized as physical adsorbents or as chemisorbents. This is simply a categorization based upon the strength of the bonding of the solute (the material being adsorbed and sometimes called the “adsorbate”) with the adsorbent. Although a great many of the most important adsorption systems fall clearly into one of these two categories, some d o not because the energy of adsorption may be between the values expected for physical adsorption and chemical adsorption. Physical adsorption is usually more common, especially for gas systems and when regeneration of the adsorbent by small changes in pressure or temperature is desired. Regeneration of chemically adsorbed materials may be difficult. Ion exchange relies upon electrostatic forces to hold cations (or anions) on/within the solid “ion exchange material.” However, the cations

30

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(or anions) in the ion exchange material can be replaced (exchanged) with other cations (or anions) in a surrounding solution.

EXAMPLES OF COMMON ADSORBENTS Activated Carbon Activated carbons, sometimes called granular activated carbons (GACs), are widely used for removing traces of nonpolar organic compounds such as oils and solvents from gas and water streams. Since control of hydrocarbon and solvent emissions and removal of oils from water discharges are common problems in waste and effluent management, these adsorbents have numerous applications in effluent treatment. They are able to reduce oil and solvent emissions in gas effluents to very low levels, and their applications are likely to increase further if emission requirements continue to be tightened. Carbon beds in air effluent streams (vent or offgas streams) can also provide protection to the environment in situations when inadvertent discharges are made to the effluent stream. The adsorption behavior of an activated carbon often results from the carbon surfaces and their normal hydrophobic (water repelling) nature. Essentially any nonpolar molecule will be adsorbed on an activated carbon, such as most common hydrocarbons, trichloroethylene, trichloroethane, dichloroethane, polychlorobiphenyls, etc., which are common pollutants. Activated carbons thus have numerous roles in environmental control because they remove organic pollutants from water as well as air effluent streams. The hydrophobic nature of carbon surfaces can be affected by reactions or chemical adsorption on the surfaces. Significant oxygen on carbon surfaces can decrease the hydrophobic properties. Even dissolved oxygen in water can affect the adsorptive properties of activated carbons for removal of certain organic contaminant, that is, contaminants that are likely to interact with oxidized sites. Nakhla and co-workers have studied the effects of dissolved oxygen on the removal of phenolic and creosolic compounds [5-81. The capacity of the carbon surface for these contaminants is increased significantly by the presence of oxygen in the water. The increases could approach 50%. Heating the carbon in a vacuum can often remove the reacted or chemisorbed materials from the surfaces and restore the hydrophobicity or the original nature of the carbon surfaces. Activated carbons are prepared by pyrolysis of natural carbon containing materials, usually woody materials. The woody material is heated to several hundred degrees Celsius in the absence of oxygen or in the

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presence of little oxygen. The material decomposes with only limited oxidation, and volatile compounds (water and other decomposition products) are driven off.The residue is a char that is mostly carbon. It will, of course, retain most of the inorganic mineral elements that were present in the original woody source material. Coconut shell is one material that pyrolyses to a particularly good activated carbon. Activated carbons may have surface areas of 100 to 1400 m2/g and are especially useful for removing hydrocarbons, including benzene and toluene, from air [9]. The surfaces of activated carbons can be altered by treatment or even preadsorption of selected materials on the carbon. With preadsorption of some materials, the selectivity of the carbon for different adsorbates can be altered greatly. A useful recent review of activated carbon adsorption and mathematical equations for designing adsorption beds has been written by Crittenden et al. [ 101. Activated carbons are sold in powdered and granular forms. The powdered form is used for single contact (single stage) operations, usually in some water treatment operations when high mass transfer rates are needed and when extremely high removal efficiencies are not needed. The powdered carbon is usually removed by filtration and discarded after a single use. Thus powdered activated carbon applications may be carried out much like precipitation operations, and even sometimes in conjunction with precipitation operations which remove inorganic contaminants while the carbon removes the organic contaminants. Granular activated carbons most often come in size fractions between 8 and 30 mesh or between 12 and 40 mesh. Granular carbons can be regenerated and reused several times. For carbons used to remove organic contaminants, thermal regeneration may be sufficient, but it is common to introduce superheated steam or even some air to the regeneration furnaces/ovens. Both tray ovens and fluidized beds have been used to regenerate activated carbons. Temperatures in the regeneration ovens or beds are usually staged to d o as much drying as possible at lower temperatures. The highest temperatures required depend upon the temperature needed to remove the particular contaminant(s) on the carbon. However, since so much of the activated carbon is regenerated in commercial furnaces at firms supplying regeneration services to several users, much of the carbon will be regenerated at rather high temperatures (near 1000°C) commonly used by commercial regenerators. Part of the carbon will be destroyed by the chemical treatment (essentially from burning), but attrition is probably the major cause of carbon loss during regeneration operations. Since regeneration usually takes place in separate ovens designed just for regeneration, it is necessary to “slurry” the carbon from the bed and transport the carbon to the regeneration ovens and dryers.

32

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This physical handling of the carbon increases the fines content, which is most likely to be “burned off” or lost during regeneration. Regeneration loss may be as much as lo%,even with well-operated systems [ l l ] . Somewhat higher losses have been reported for other systems. Regeneration usually affects the properties of the carbon. As noted, part of the carbon is effectively burned, and regeneration is likely to increase the pore sizes and even the surface area of the carbon. These factors can enhance the performance of the carbon, and in many cases regenerated carbon may perform better than the original carbon. However, regeneration can affect surface chemistry of the carbon, producing unfavorable changes in carbon performance. Oxidation and reactions with steam can lower the carbon hydrophobicity, which usually needs to be restored before the carbon is put back into use. Restoration is usually done through a final stage of regeneration in which the carbon is heated in the presence of low concentrations of air (oxygen) or water. Generallx one can expect the capacity of carbons to be near 90%of the original capacity after regeneration. As noted, regeneration can be performed in house, or the spent carbon can be sent to a commercial firm that specializes in regeneration of activated carbons. Such firms are often the original suppliers of the carbon. The choice of going off site to have the carbon regenerated is usually made when there is not enough supply of spent carbons on site to justify a separate regeneration system. One estimate gives approximately 100 kg/day as the regeneration rate when one is likely to find on-site regeneration more economical [ 121. For smaller adsorption systems that require a lower rate of carbon regeneration, off-site regeneration is more likely to be the preferred and more economical choice. When considering on-site regeneration systems, remember that extensive off-gas treatment may be required for the regeneration ovens, and the capital costs may be relatively high. Although there may be several environmentahvaste applications where one would want to regenerate carbon on site, there will probably be far more cases where carbon beds would operate on dilute streams for relatively long times between regenerations, and there will not be enough regeneration needed to justify an on-site regeneration facility.

Organic Polymers Some organic polymers have been used as adsorbents for organic vapors or dissolved organic compounds. Many of them are polystyrene-divinylbenzene (DVB) copolymer spheres much like the basic support structure of ion exchange materials that will be discussed later. However, for adsorb-

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ing organic compounds it is not necessary to form the ionizable groups on the polymers that give the ion exchange properties. Some of the applications for polymer beads are similar to those for activated carbon. Because of the extremely high surface area of some activated carbons, polymer beads are more likely to have lower total capacities than many activated carbon adsorbents [ 13,141. The principal advantage of polymer adsorbents is the ease of regeneration and the relatively small loss in adsorption capacity with each regeneration cycle. One study of chlorobenzene and benzoic acid removal from water using Dow Chemicals XUS resin beads showed capacities to a few hundred grams per liter of bed (determined from the 50% breakthrough curve, an approach to estimating adsorbent capacity that will be discussed later) when removing the contaminants from concentrations of 250 to 300 ppm in water. Both contaminants could be removed from the polymer with a small volume of methanol, approximately 10 to 20 times the volume of the adsorption bed. Since polymer adsorbents are usually hydrophobic, they are often difficult to wet when they are used to remove organic contaminants from water streams. A pretreatment with methanol can allow the polymer adsorbent to be wet by water, and the methanol can be displaced by the organic contaminant that will be removed by the polymer subsequently. Note, however, that there will be a release of a small amount of methanol to the water effluent if this approach is used. Equilibrium adsorption of organic contaminants by organic polymers can be complex and may not follow the behavior predicted by the more common isotherms used for more rigid adsorbents (Langmuir, Freundlich, etc.). The different behavior can be even more different in multicomponent systems. The different behavior results at least in part from swelling of the polymer particles as the organic contaminant loading increases. While the presence of a second adsorbate usually decreases the adsorption capacity of rigid adsorbents for the contaminant(s) of interest, the presence of a second adsorbate could swell the resin and increase the capacity of the polymer adsorbent for the contaminant of interest. This effect could be thought of as dissolution of the contaminant in the adsorbed second adsorbate. Some readers may notice that this could be called adsorption if the contaminant dissolves in the second adsorbate, or even in the polymer itself. In this book, this will still be considered adsorption since it involves removal of the contaminant to a solid, whatever the mechanism. With suitable active groups attached to the polymers they can be used as ion exchange materials, but some of those materials can also be useful adsorbents. Polymers with amine groups can remove acid gases

34

CHAPTER 2

from effluent streams [15]. Of course, organic polymers are not stable at high temperatures, and they do not retain some acid gases at very high temperatures. Polystyrene-DVB polymers with amine groups can remove acid gases such as SO, and NO, at near ambient temperatures, and the gases can be removed by heating the adsorbent to temperatures approaching 100°C. Although SO, can be removed from gas streams and regenerated effectively at modest temperatures with primary, secondary, or tertiary amines, NO, is difficult to remove from resin adsorbents with either primary or secondary amines. Remember that carbon dioxide is also an acid gas and can be adsorbed on resins with basic groups such as amines. However, the adsorption of carbon dioxide on resins with tertiary amines is not great [ 161. Carbon Molecular Sieves Carbon molecular sieves are receiving increased attention, but their costs exceed those of the more common granular activated carbons. Like activated carbons, carbon molecular sieves are prepared by carbonization of carbon containing materials. The difference in the preparation is that the molecular sieves are prepared from chemical compounds (usually polymers) while activated carbons are prepared from natural materials. The homogeneity of the polymers results in a much more narrow range of pore sizes, and the pore size peaks at a significantly smaller size than the pores in activated carbons. The surfaces of carbon molecular sieves are hydrophobic, like those of activated carbons. Furthermore, since the carbon molecular sieves take the same shape as their polymer precursors, it is relatively easy to form them into a variety of shapes. Other than spherical or granular the most interesting shape is probably fibrous. Fibers can have small diameters and be woven into larger threads or even into fabrics. The term “molecular sieve” describes the uniform and small pore sizes. The term was used earlier to describe zeolites and implies that the size distribution is narrow enough to “sieve” out larger molecules and thus permit only molecules under a given size to be adsorbed. However, the very small pores of carbon molecular sieves are still significantly larger than the pores of zeolites. Since many solutes have molecules significantly smaller than the pores of carbon molecular sieves, it is probably better to avoid thinking of them as sieves, but simply as high surface area carbon adsorbers with relatively uniform size and very small pores. Pore diameters can play important roles in the relative adsorption equilibrium of different contaminants and provide extremely high internal surface areas. For instance, one study of phenol compounds on fibrous carbon molecular sieves showed that 4-nitrophenol adsorbed more strongly than

ADSORPTION AND ION

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35

4-chlorophenol, which adsorbed more strongly than phenol [ 171. However, one earlier study [ 181 found the opposite order of adsorption preference. This could have resulted from a dependence of selectivity on pore diameter, but it is also possible that trace components or differences in the surface structure of the different materials also play a role.

Silica Gels Silica gels are inexpensive adsorbents for removing water and other h y drophilic materials from gases. They are silica polymers dehydrated into an inorganic gel and are usually produced from alkali metal silicates. Silica gels have effective pore diameters of approximately 5 to 50 d;, usually with a peak in the size distribution near 20 A. They are available in several particle sizes and are usually produced in approximately spherical shapes. The most common application for silica gels is in the removal of water, but that is not usually a major problem in environmental and waste processing. With only modest difficulty and expense, however, other polar molecules can be attached to silica gels with polar or silane bonds. Such attached molecules can incorporate a variety of specific chemical groups which completely change the adsorptive properties of silica gels; some attached groups can even make the silica gel hydrophobic. Silica gels are also useful solid substrates for incorporating ligands that are highly selective for individual solutes such as metal ions. Many ligands can be easily attached to silica through silane bonds. These can become highly specific adsorbents or ion exchange materials capable of removing (largely) individual components or groups of components from complex mixtures. Some such treated silica particles are relatively expensive for large-scale operations, but with increased use and high production rates their cost could decline, perhaps considerably.

Zeolites Zeolites are aluminosilicates with regular porous crystal structures [ 191. Although zeolites occur naturally, a wider variety of zeolites are manufactured. All zeolites are constructed from a few crystal units, but the pore structures can differ considerably because the units can be assembled differently in the crystals. Aluminosilicate structures carry a net negative electrical charge that is neutralized by a cation. Further differences in zeolites can result when different cations are added to neutralize electrical charges on crystal unit surfaces.

36

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The most common group of zeolites is type A. AU type A zeolites have the same crystal structures, but they may have different cations on the unit surfaces. Type 5A zeolites have Ca2+ ions on the surfaces and pore sizes just under 5 A. Type 4A zeolites have Na+ ions on the surfaces and slightly smaller pores. The less common type 3A zeolites have K+ ions on the unit surfaces and even smaller pores. Type X and type Y zeolites have more open structures and larger effective pore diameters of approximately 8 A. More recently, more zeolite structures have been synthesized, usually with even larger pores. The initial use of a new zeolite is likely to be in catalysis if the costs are relatively high. However, if (or as) the costs of new materials decline, they may be considered for use as adsorbents. Because zeolites have crystal structures and the pores are an integral part of those structures, the distribution of pore sizes is very narrow. Although each pore will be essentially like another, it is too simplistic to view the pores as straight cylindrical holes. A more realistic image of zeolite pores is a series of interconnected chambers with restricted openings. Although all chambers and openings may be identical, they are not described so neatly by a single pore diameter. The most important dimension is usually the size of the opening to the chambers. As noted, that dimension is affected when the cation that neutralizes the electric charge of the aluminate structure is changed. Different zeolite types have different pore dimensions. v p e A zeolites have the smallest pores of the common zeolites, and type Y zeolites have the largest pores of the common zeolites. Some newer zeolites have significantly larger pores, but they are not commonly used as adsorbents. Effective pore size is determined by the structure (type) and the number of neutralizing cations in it, and the effective size of the pores can be altered by changing the neutralizing cations. For instance, one study found that the adsorption of some compounds by Na-Y zeolite could be altered significantly by preparing the zeolite with some sodium ions replaced by lithium ions

POI.

Diffusion rates into the small pores of molecular sieves are usually very slow because of the small effective pore size, and it is necessary to use very fine zeolite particles to obtain satisfactory adsorption rates for most applications. However, small adsorbent particles cause an excessive pressure drop in packed beds when high processing (flow) rates are needed. To gain the advantages of both large adsorbent particles (a low pressure drop or high throughput) and small zeolite crystal sizes (high adsorption rates), commercially prepared zeolite adsorbents usually consist of very small zeolite crystals bonded into much larger overall adsorbent particles. The crystals are usually held together by a clay binder. Diffusion coefficients through the larger openings between the zeolite crystals are

ADSORPTION AND

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relatively high because the openings are much larger than the molecular dimensions of most adsorbing materials, and the pore walls do not greatly restrict molecular motion (diffusion). Diffusion coefficients within the zeolite crystals remain very small, but the diffusion paths are short because of the small crystal sizes. There will, of course, be a significant reduction in the effective diffusion coefficient even in the macropores between the crystals from the diffusion coefficients in the surrounding fluid simply because of the random direction of the pores and the presence of “dead end” pores. These effects are usually grouped into the “tortuosity factor,” which decreases the effective diffusion coefficient approximately two- to six-fold below that observed in a free media. Such adsorbents constructed with two size pores are often called “bidispersed” pore systems. That is, their behavior is governed by two pore sizes, namely the size of the opening between the zeolite crystals (held together with clay binder) and the size of the openings within the zeolite crystals. Under some conditions, the adsorption rates may be controlled by diffusion rates in the zeolite crystals (micropores); under other conditions, the rates may be controlled by diffusion through the larger (macro-pores) openings outside the crystals; and under still other conditions, the diffusion resistance in both pore sys100tems may contribute to the adsorption rates. This will be discussed in more detail later. The inorganic and ionic structures of zeolites make them particularly good adsorbents for polar materials, especially moisture (water) from gases and nonpolar liquids such as hydrocarbons and oils. They have such a high affinity for water that temperatures of approximately 200 to 400°C are required to desorb the water. The temperature and desorption time required depend upon the degree of desorption needed. For extremely effective regeneration, even higher temperatures and longer desorption times (hours) may be required. Such levels of desorption are needed when the zeolite is to be used for reaching extremely low moisture contents in the gas or liquid. Since the strong affinity of zeolites for water makes desorption inherently costly in energy and time, zeolites are more likely to be used only where very high dryness is required; even then, they may be used only for the final polishing step. Type 5A and type 4 A zeolites are especially effective in removing water. As noted, drying is not one of the most common applications for adsorption in waste management and environmental management, but zeolites could also be used to remove other polar materials that contaminate gas or liquid effluents or products. However, remember that they are likely to remove water as well, so any moisture present will consume

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2

some of the adsorption capacity of the zeolite adsorbents operating on gaseous streams. Zeolites can also be used as ion exchange materials because the cations neutralizing the net negative charge on the crystal faces can be exchanged. Use of zeolites in ion exchange will be described later.

Natural Products as Adsorbents Several natural materials have been, or can be, used as adsorbents with little or no treatment. Some of the original adsorbents were natural materials, and synthetic materials became more commonly used as their properties improved. Eventually many of the synthetic materials became more effective than the original natural materials. As noted, the first zeolites used in adsorption were natural minerals, but synthetic zeolites have gained most of the high performance markets. Coal and plant materials have been used as adsorbents, and almost any biomass created by microorganisms can adsorb or undergo ion exchange with some metal ions. Useful adsorption by these materials can occur in situations when it is not even fully recognized. The adsorption of contaminants by the biomass in activated sludge digesters in municipal sewage plants is one example. There is a growing interest in making better use of the capabilities of low cost natural materials such as adsorbents, particularly for waste treatment. In some ways it is difficult to draw a clear line between “natural” and synthetic adsorbents since many of the most effective and widely used adsorbents are “derived” from natural materials. As noted, activated carbon is prepared from wood or coconut shells. When a natural material undergoes significant processing or treatment, it is not clear if it should be considered as a natural or a synthetic adsorbent. In many high performance applications, synthetic or highly treated adsorbents are likely to prove superior to untreated natural materials. However, when a very inexpensive natural material is sufficient, it should be considered. In recent years there has been interest in materials such as biomass and microorganisms (alive or dead) for removing materials such as heavy metals from aqueous wastes. As noted earlier, there has also been a growing recognition that adsorption on biomass can occur in other equipment, such as sludge digesters, which are not known principally as adsorbers, and affect its performance. Special biosorption equipment and operations also have been studied extensively, but few systems are known to be operating in the United States. However, there appears to be more interest in Europe [Zl).It is difficult to know exactly why biosorption is not used more extensively in the United States. Expected difficulties with handling or disposing of the solid biomass after its use

ADSORPTION AND

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can be one problem. Incineration, rather than regeneration, appears to be an attractive way to destroy the relatively inexpensive spent adsorbent, but approval of incineration permits is difficult to obtain in the United States. The reliability (or lack of reliability) of living systems may also play a role in discouraging adoption of biosorption processes. ION EXCHANGE MATERIALS Solid ion exchange materials are insoluble solids with ionized groups located on the surface or in interior regions that can be reached by the fluid. For most practical purposes, the ion exchange systems discussed are used to exchange ions from aqueous (water) solutions. The ion exchange materials may be naturally occurring materials such as zeolites, a modified natural material such as sulfonated coal particles, or a synthetic material fabricated specifically for its ion exchange capabilities. Although the original ion exchange materials usually were derived from natural materials, the ability to synthesize materials with better properties has resulted in an industry dominated by the (usually) superior synthetic materials. Synthetic ion exchange materials can be made of either organic or inorganic components. The most common materials are organic polymers (resins) with ion groups placed along the polymer chain. This permits the placement of numerous ions in the polymer and thus gives high “capacities” for ion exchange. The polymers are usually cross-linked sufficiently to make them essentially insoluble in water, even with the large number of ionized (polar) groups, and to give them structural strength. Without the ionizable groups, such polymers would be dense, and water would not penetrate the polymer particles significantly. However, when the ion groups are attached to the polymer, the particles swell from osmotic forces, and water penetrates the resin (polymer) particles. Water penetration permits the ions neutralizing the fixed charges on the polymer to move relatively freely and rapidly and thus to exchange places with other ions in the external solution. It is common to think of exchangeable ions in the resin (polymer) being attached or associated with a specific charged group fixed on the polymer. We often write expressions to describe ion exchange that look like chemical reactions: M: + M * R 5 M: + M ~ R

(1)

where Mf and M t are metal ions and R is a resin site with a charge opposite to that of the exchanging ions. (In this equation, both metal ions are monovalent.)

40

CHAPTER 2

- CH,-

- CH, - CH,-CH-

-

3Qc; CH

SOj-

SO,-

CH,

- CH,-

CH

so

j-

H+ n+ H+ FIGURE 3 Chemical structure of a common polystyrene-basedion exchange resin with sulfonic acid groups, a strong acid cation resin.

In some cases, such as hydrogen ions neutralizing the charge of weak acid groups on the polymer, this may be a realistic view of the material: hydrogen ions are less free to “roam” in the water that penetrates the polymer. However, in many cases, especially those involving other neutralizing cations such as metal ions, the neutralizing (or exchangeable) ions may roam freely in the penetrating water. Then osmotic swelling is significant and limited only by the restraining force of the “stretched” polymer, which equals the osmotic pressure. In these cases, it is probably better to view the resin polymer as a concentrated solution with one set of ions free to migrate and the other fixed or restrained in spacial position because it is part of the polymer. Thus, a sodium ion in such a cation resin may have little more association with any particular negatively charged groups on the polymer than with any other negatively charged group on the polymer. Statistically, there will be a higher probability or concentration of mobile ions around the fixed ions of opposite charge, but individual mobile ions move randomly throughout the region by thermal motion. An ion exchange material can be a cation exchanger (exchange cations) or an anion exchanger (exchange anions). Since the exchanging ions are mobile, a cation exchanger has negatively charged anion groups incorporated (fixed) in the polymer, and an anion exchanger has positively charged cation groups incorporated in the polymer. One well-established and common group of synthetic organic polymer-based ion exchange materials is constructed of polystyrene polymers with divinylbenzene cross-linking. It is relatively easy to incorporate ionic groups into the polymer, usually on the benzene groups of the polystyrene (Figure 3). If sulfonic acid groups are incorporated, the material is a “strong acid” cation exchange material. The ion exchange capability results because the hydrogen ions from the acid are ionized, leaving the

ADSORPTION AND

ION EXCHANGE

41

negatively charged sulfonate group fixed on the polymer. It is called a strong acid ion exchange material because the sulfonic acid is a strong acid and is, thus, essentially completely ionized over the entire pH range likely to be of interest, even at low pH (in acid solutions). On the other hand, if a carbolic acid group were incorporated in the polystyrene polymer, the material would be a “weak acid” cation exchange material. The hydrogen ions of carbolic acids can be exchanged, but with more difficulty. The hydrogen ions will not be completely ionized in low pH (acid) solutions. Thus, one basis for characterizing cation exchange materials is by the strength of the acid group incorporated in the polymer structure. To create an anion exchange material, it is necessary to incorporate an ionizable basic group to the polymer. The ionized hydroxyl ion can then be exchanged with other anions in the solution. Amine groups are bases that are usually incorporated on polystyrene polymers. Again, the anion exchange materials may be classified as strong bases or weak bases, depending upon the strength of the base group incorporated in the polymer. Quaternary amines are strong bases, and the hydroxyl ions can be ionized at essentially any pH. Strong base anion exchangers are often I1 materials. Both of these “types” of resins classified as lLpe I or use quaternary amines and are considered “strong base” resins, but the two types use different components on the quaternary ammonium group. ’Qpe I1 resins are slightly weaker than ‘Qpe I resins. However, if ternary amines (or even secondary amines) are built into the polymer, the material will be a “weak base” anion exchange material because these groups are weak bases. That means that hydroxyl ions will not be fully ionized at high (basic) pH. The standard polystyrene-DVB resins and many other polymer resins are approximately homogeneous polymers that swell when placed in water or other aqueous solution. The degree of swelling depends upon the degree of cross-linking and the solution concentration. For weak acid or base resins, the swelling can also depend upon the concentration of hydrogen or hydroxide ion. For ions to exchange, they must diffuse through the swollen polymer structure. These diffusion rates can be relatively low because of the small spaces between polymer chains, that is, low compared to diffusion rates in water. Improved mass transfer rates can be achieved if larger pores can be created within the resin, and many of the more recent resins are constructed in this manner [ 221. One common way to construct such resin particles involves first producing very small, and preferably uniform size, particles. These small particles can then be clustered into larger overall size particles. This results in two principal size pores: small pores within the small particles, and larger pores between the small particles within the clusters. This is similar to the structure of zeo-

me

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FIGURE 4 Micro-pore and macro-pore structures of adsorbents and ion exchange materials. Example structure of larger particles that are clusters of porous smaller particles. Micro-pores are within the smaller particles; macro-pores are spaces between the smaller particles.

lite adsorbents discussed earlier with binders holding together very small particles of zeolite crystals. Even greater porosity can be achieved by forming intermediate size clusters of the small particles and larger clusters of the smaller clusters. This results in at least three groups of pore sizes: pores within the small particles, pores in the small clusters between the small particles, and larger pores in the larger cluster between the smaller clusters (Figure 4). More recently there have been smaller quantities of relatively costly ion exchange resins constructed with the resin coating porous structures of rigid materials such as silica, but these materials are not likely to be useful for large-scale operations until their cost is reduced significantly. Although the polystyrene-DVB-basedpolymers have been standard materials for several decades, manufacturers have made significant improvements in the structure of the materials and in the polymer and ionic groups used. Table 1 lists a few common organic-polymer-based ion exchange materials from major U.S. manufacturers. The type of resin refers to whether the resin is a strong acid, strong base, etc. AU strong base resins are v p e I1 unless specified in the table. Some of these materials may be used for a variety of ion-exchange-based separations, but others were developed for properties needed in specific applications.

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TABLE 1 Some Exmples of Ion Exchange Resin Manufacturers and Resins Manufacturer and resin name Dow Chemical Dowex 50 Dowex 1 Dowex 2 Rohm and Haas Amberlite 200 Amberlite IRC76 Amberlite IRC900 Arnberlitr 1RC93 Sybron Chemicals IONAC C-249 IONAC CFPllO IONAC CC IONAC ASB-1 IONAC A-641 IONAC AFP-329 Purolite Resins Purolite C 100 Purolite C 105 Purolitc A 400 Purolite A 100

Resin type

Comments

Strong acid cation resin Polystyrene DVB Strong base anion resin Polystyrene DVB Weaker base anion resin Polystyrene DVB

Available in a variety of crosslinkage values and sizes Available in a variety of crosslinkage values and sizes Available in a variety of crosslinkage values and sizes

Strong acid cation resin Polystyrene DVB Weaker acid cation resin Acrylic Strong base anion resin Polystyrene DVB Weak base anion resin Polystyrene DVB Strong acid cation resin Polystyrene DVB Strong acid cation resin Polystyrene DVB Weak acid cation resin Acrylic Strong base anion resin Polystyrene DVB Strong base anion resin Polystyrene DVB Weak base anion resin Polystyrene DVB Strong acid cation resin Polystyrene DVB Weak acid cation resin Acrylic Strong base anion resin Polystyrene DVB Weak base anion resin Polystyrene DVB

Macroreticular

Macroporous

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This table should not be viewed as complete, and new resins are being developed annually The length of the table should not be considered as an indication of the complete variety of resins sold by a vendor or the volume of resin they manufacture. The tables show examples and indicate the variety of ion exchange resins available. Before proceeding too far in developing an ion-exchange-based waste separation facility it would be wise to consult the manufacturers to determine what new materials are available that may be more suitable for the application and to obtain data or run tests with the resins and solutions of interest. Some resins come in a variety of particle sizes, but the most common size for larger-scale applications is about 0.5 mm in diameter, optimum for many applications. Smaller particles give higher mass transfer rates, but larger particles require less pressure drop for pumping the liquid through the beds. Smaller particles are likely to be desired for analytical chemistry and laboratory applications, especially for liquid chromatography. Largescale industrial applications are likely to need somewhat larger particles to achieve high throughput. One group of inorganic materials that have important ion exchange capabilities has been discussed as adsorbents, namely zeolites. In aqueous solutions, the cations can be exchanged; thus, zeolites can function as cation exchange materials. Remember, zeolite structures carry negative charges neutralized by metal cations at specific crystal faces. The different metal cations distinguish one type A zeolite from another. The size of the cation (and the number of cations required to neutralize the charge) determines the size of the cavity entrances through which molecules must pass if they are adsorbed. Because zeolite structures (crystals) have small openings, migration of ions through the structures to exchange ions can be much slower than diffusion in some organic-polymer-based ion exchange materials that can swell to give relatively large openings. The use of inorganic materials such as zeolites may, nevertheless, be favored over organic materials where slightly higher temperatures, oxidizing conditions, or radiation fields are required since those conditions can degrade organic materials rapidly There are also cases where zeolites have better affinities (selectivities) for specific ions [ 231. Several other inorganic materials have important ion exchange capabilities. One large class of materials is the hydrous oxides of metals such as aluminum or zirconium. These materials may be amphoteric and act as anion exchange materials at low pHs and cation exchange materials at high pHs. Even silica gel can have significant ion exchange capacity. A notable book that summarizes early work on inorganic ion exchange was written by Amphlett [ 2 4 ] .A review of inorganic ion exchange was edited

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TABLE 2 Examples of Inorganic Compounds That Can Be Used as Adsorbents or Ion Exchange Materials Alumina Ammonium molybdophosphate Antimonate acid Barium sulfate (activated by calcium) Cobalt hexacyanoferrate (with potassium hexacyanoferrate) Copper oxide Ferric hydroxide Magnesium oxide Manganese dioxide Nickel hexacyanoferrate (withhithout manganese dioxide or potassium hexacyanoferrate) Silica Sodium titanate Tin antimonate Titanium antimonate Titanium dioxide Titanium phosphate Zinc oxide Zinc titanate Zirconium oxide Zirconium phosphate

by Qureshi and Varshney [ 2 5 ] . This book focuses on applications in analytical chemistry, but there is a good review of properties that could be helpful in other applications. Significant advances have been made in the development of inorganic ion exchange materials during the last three decades, and there is now a far wider range of materials studied and used. High selectivity can be achieved in inorganic ion exchange materials by selecting the geometry of the internal cavities of the material as well as the active groups that provide the negative or positive sites for attracting cations or anions that can be exchanged. A partial list of some of the minerals whose ion exchange properties have been studied is given in Table 2. One should not think of these as simple compounds because the structural properties of the materials can sometimes vary considerably with change in the preparation procedures. Layer spacing of clay or other layered materials or the pore size or other internal material shapes can affect the selectivity of the material for different ions. Commercial materials are now available that are prepared by proprietary methods to enhance their selectivity for ions

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TABLE 3 Examples of Common Adsorbents ~

Adsorbent

Notable properties

Applications

Activated carbon

Hydrophobic surfaces Low cost

Silica gel

Hydrophilic surface High capacity (for drying agents) Surfaces can be made hydrophobic Hydrophobic surface

Removal of organic pollutants from air or water Drying gases or organic liquids

Activated alumina Zeolites (molecular sieves)

Carbon molecular sieves Organic solids (polymers) Reactive (irreversible) adsorbent

Very hydrophilic Uniform pores Lower capacities than silica gel or activated alumina Hydrophobic surfaces Approximately uniform pores Moderately expensive Hydrophobic internals More expensive than carbon Reactive surfaces Specific to some contaminants

Drying of gases or organic liquids Drying of gases of liquids Separation of gas mixtures

Gas separations

Removal of organics from gases Removal of trace contaminants Usually not cost effective for removing more than trace quantities Often used for strong acid or reactive contaminants

of importance. Clearfield discussed some of the more recently studied materials [261. A new concept for adsorption and ion exchange systems is the use of monoliths of adsorbent material rather than randomly packed particles. Although such a material could be constructed of many different materials, some of the initial interest comes from the use of inorganic materials. Monoliths can have interesting properties, especially potentially low pressure drops, but more will be said about monoliths in the next section.

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Structure of Ion Exchange Materials and Adsorbents

The basic shapes of organic-polymer-based ion exchange materials are usually spherical, but other shapes, such as thin membranes, have been prepared. The particles are usually formed in a continuous range of sizes, and selected “cuts” of different narrow size fractions are separated and marketed separately. Smaller .particles are desirable to achieve rapid exchange rates because the distance for the exchanging ions to diffuse is shorter than for larger particles. However, smaller particles offer greater flow resistances, and ion exchange column design, like adsorption, involves selection of optimal particle sizes that permit acceptable exchange rates without an excessive pressure drop. ’Itvoimportant physical properties of organic gel ion exchange materials are their tendency to swell or contract as the solution changes and their possible deformation under pressure. Swellinglshrinking occurs when the ionic strength of the solution around the resin is changed or, in weak acidbase ion exchange materials, when H+ or OH- ions are loaded or eluted from the resin. Such changes usually occur between the loading (operating) and unloading (regeneration) cycles. Ion exchange operations are likely to be carried out on dilute waste streams, and the loading cycle can be relatively long if the concentration of the ion to be removed is sufficiently dilute. However, it is usually desirable to recover the ions at higher concentrations. This means that more concentrated regeneration solutions are likely to be used. Gel-type ion exchange resins will shrink when regenerated with more concentrated eluate solutions and expand again when placed back in operation with a dilute feed stream. If a low ionic strength water wash is used between the regeneration and operating cycles, resin swelling could be even greater. In most cases, swelling and shrinking is not a major problem if sufficient excess bed volume is provided to accommodate for the swelling. Changes in the resin volume can generate some mixing of the resin between cycles, but that is not a major problem for all applications. If the resin does not expand/contract smoothly, variations in the void fraction and, thus, nonuniform flow could result. This could have serious effects on bed performance. Since gel-like ion exchange resin particles are compressible, they can also deform in packed columns under pressure. The pressure is usually that imposed by resistance to flow through the column. The force on the resin particles is proportional to the pressure gradient, and resin deformation then increases as the flow rate is increased. Smaller particles can withstand higher pressure gradients better than larger particles, but, of course, smaller particles also require greater pressure gradients to sustain a given slow rate through the column. Deformation of the resin

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particles will cause the resin to “fill” part of the void volume in the bed and increase the flow resistance (or pressure drop) for a given fluid flow rate. Increasing the cross-linking of the gel polymer increases the strength of the particles against deformation as well as strength to resist swelling. When high flow rates and thus high pressure gradients are required, low cross-linked resins are not likely to be satisfactory. However, higher crosslinking also results in slower diffusion of ions within the resin and thus lower mass transfer rates. The best cross-linkage to use is determined from an optimization between resin strength (ability to withstand pressure gradients), mass transfer rates, and difficulties in bed packing that result from swellinglcontracting during regeneration cycles. Many newer resins have more complex internal structures than the gels just described. Usually the spherical external shape is retained, but several advantages can be achieved by altering the internal structure of the particles. Generally, the two most common reasons for developing more complex internal structures are to increase diffusion rates and to achieve stronger particles. In many cases, the resulting material makes improvements in both properties. Diffusion rates within ion exchange materials can be relatively slow, especially when high cross-linkage is needed for strength, and the most common approach to alleviate this problem is to prepare larger particles that are made from very small particles assembled into large structures, much like the synthetic zeolite-binder structures described earlier. Such structures are sometimes called “bidisperse” or “macro-reticular.” The important feature is the large pores (usually the space between the smaller subparticles) and smaller pores within the “subparticles.” As with the zeolites, diffusion rates into the smaller subparticles can be rapid because the diffusion paths are short, but the pressure gradient down the column is set by the size of the much larger aggregate particles, not by the size of the small crystals. A variety of inorganic and organic materials can be used to bind small “subparticles” into aggregate particles. Cellulose and polyacrylonitrile (PAN) [27-29] are examples of polymer gels used with considerable success. Macro-reticular resins with rigid binders also are often stronger and less prone to swelling than “homogeneous” gel particles. However, some organic binding materials such as cellulose or PAN can also be “soft” and have no more than moderate strength. Organic resins can also be prepared on strong inorganic substrates of silica or alumina to give even greater strength. Many high performance ion exchange resins have been prepared for small analytical chemistry scale operations, but the costs for many of these resins are likely to be too high for use in high throughput wastewater treatment operations. Some such materials are more likely to be used on a preparative (production) scale in biotechnology and in

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the pharmaceutical industry, where high value products are involved and where the scale of operations is relatively modest. These industries also are often interested in large molecules that have especially low diffusion coefficients in conventional ion exchange resins. As the use and demand for high performance resins increase, the scale of operations used in their preparation will increase, and that could result in some cost reduction. As the merits of high performance resins become more evident, new and less costly preparation methods may be developed. However, large-scale waste handling operations are likely to remain the domain of relatively cheap conventional resins for at least several years. Diffusion rates in inorganic materials can be particularly slow because the pores (or plate spacings) are often very small, so it is often necessary to keep the diffusion paths short and adopt a macro-reticulartype structure. Small particles of the ion exchange material also can be incorporated into larger agglomerates with the spacing between the small particles sufficiently large that the diffusion rates in the macro-pores are relatively high. It is especially desirable to incorporate smaller inorganic ion exchange materials into “engineered forms” with clusters of very small particles. Several approaches are used to “bind” the smaller particles together. Zeolites are often produced in spherical or granular (or other shapes) by using clay binders to hold the zeolite particles together. As the macro-pores in a macro-reticular structure become sufficiently large, the effective apparent diffusion rate within the macro-pores can become very high and even appear to exceed the diffusion rates of the ions in water (and the same phenomena can occur with adsorption in macro-reticular adsorbents). This occurs because, as the pores become sufficiently large, ions begin to be transported through the pores by convection (flow) as well as by diffusion. These phenomena were discussed by Watson [30,31] and Carta [32]. The apparent macro-pore diffusion increases with fluid flow rates through the bed because the increasing pressure gradient forces fluid through the pores at increasing rates, and the contribution of convection to the mass transfer becomes increasingly important. Of course, the actual diffusion coefficient does not exceed that in water, but the apparent diffusion rate can exceed the rate calculated by ignoring the effects of convection within the particles. Adsorbents and ion exchange materials with very large pores and small micro-particles are likely to become more common, but the growth in their applications probably will begin in those cases where the value of the product can justify the use of new and, often, more expensive adsorbents and ion exchange materials. Since the vast majority of adsorbents are spherical or granular shaped, and granular shapes are usually considered “near spherical,” it is unusual

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to even mention other adsorbent shapes. However, this could be another topic where advances may be made in adsorbent development during the coming decades. The need for short diffusion lengths has already been discussed, and the coupling between short diffusion paths and particle size has been broken by developing composite particles with very small particles agglomerated into larger particles. However, the diffusion path can also be decoupled from the flow resistance (pressure drop) in other ways, but these have not all been explored fully. For instance, by using fiber-shaped adsorbents, the diffusion length is the radius of the fiber, and the pressure losses are related to the packing density of the fibers, not the diameter of the fibers. Packed beds of spheres or granules all have void fractions that are not far from 0.5, but with fiber beds the void fraction can be varied over a wide range by changing the number of fibers per unit volume. Very high void fractions, and thus very low pressure losses, can be achieved in fiber beds if needed. Although fiber beds are not common for adsorption, they are being studied [331. Other adsorption shapes can be considered. For instance, solid monoliths with carefully formed flow channels and thin adsorbent “walls” between the channels may be constructed in the future to give low flow resistance, high mass transfer rates (short diffusion paths), and minimal flow dispersion. Straight channels through a monolith of a solid adsorbent will give lower pressure drops than packed beds of similar size particles. The mass transfer performance from monoliths, however, may not be as good as that of packed beds unless the size of the channels is reduced and the number of channels is increased appropriately. If monoliths are significantly more expensive than granular adsorbents, the initial applications of high performance adsorbent structures may be limited to high cost operations, usually the purification of high value products.

ADSORPTION EQUILIBRIA To predict how an adsorber will perform, it is first necessary to understand how much of a toxic or valuable material will be adsorbed at a given concentration (or pressure) in the fluid phase and at a given temperature. If the adsorbent adsorbs more than one component from the fluid, the adsorption of each component may be a function of the concentration of any of several components in the fluid. Those are usually referred to as multi-component systems, meaning multiple adsorbable solutes. Of course, single solute systems are simpler and the most thoroughly studied. Multiple solute problems are not only more complex but are likely to be more specific for each application and to require more data

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C

FIGURE 5 (a) Linear adsorption isotherm. (information) to understand. Thus, each multi-component system may be of interest to only a few people. The following discussion will begin with the single adsorbate systems. The equilibria will usually be discussed in terms of “isotherms.” These are equilibrium curves for constant temperatures. The isotherm will usually give the amount of the adsorbate adsorbed per unit mass (or volume) of adsorbent as a function of the concentration or pressure of the adsorbate in the fluid. The term “isotherm” apparently arose from the frequent use of adsorption to remove components from gases where the equilibrium is strongly affected by the temperature and the pressure of the adsorbate in the gas. Although all adsorption phenomena are likely to be affected by temperature, liquid-solid adsorption systems are less likely to be operated over a significant range of temperatures and may show less dependence upon temperature. Nevertheless, “isotherm” is frequently used to describe adsorption equilibria for liquid as well as gas systems, and the term will be used in the following discussions. Linear Isotherms

The simplest shape for equilibrium isotherms is a straight line, a linear isotherm. Actually this is a common shape of the isotherm for dilute systems. The linear isotherm corresponds to a constant distribution coefficient (the ratio of the concentration on the solid to the concentration in the fluid) (Figure 5a). It implies that a molecule of an adsorbate has a given probability of being adsorbed that is independent of the concentration of the adsorbate (solute). This is often the case when the loading of the adsorbate is small. The active sites, surface, or volume of the adsorbent are

52

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kC

2.0

1.5 Q&Ud

1.o 0.5 0

0

0.5

1.o

1.5

2.0

C

(c) FIGURE 5 (b) Langmuir isotherm. This example illustrates the shape of Langmuir isotherms but is “normalized,” showing the adsorbent loading in the vertical axis as a fraction of its maximum (total) capacity and the concentration normalized by multiplying by the Langmuir constant, k. (c) Freundlich isotherm. This example illustrates the shape of a Freundlich isotherm for a system with a Freundlich exponent of 0.6. The adsorbent loading is shown as the actual loading divided by the Freundlich constant, K.

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largely unfilled with adsorbates, so the chemical activity of the adsorbent surface is approximately constant. Even when an adsorption isotherm is not linear, it may be approximately linear over the concentration region of interest. That region is simply the range of concentrations from the minimum concentration up to the maximum concentration of the adsorbate expected. For the simple operation where a single adsorbate is removed from a fluid stream with a constant inlet composition, the maximum concentration is the inlet concentration. The minimum concentration is likely to be the concentration in the fluid that would be in equilibrium with the original adsorbent; if the adsorbent originally contains no solute (adsorbate), the minimum concentration will be zero. Even when the isotherm is not exactly linear over this range there may be merit in approximating the isotherm as linear because subsequent treatment of adsorption rates and bed behavior is less complex for linear isotherms.

Langmuir Isotherm Deviations from the linear isotherm can result from a number of causes. Activity coefficients (fugacity coefficients for gases) may be dependent on the concentration, and that can cause some variation in the isotherm behavior. However, even with constant activity coefficients, deviations from the linear isotherm are likely to occur at high adsorbent loading because the available active sites (or surface or volume) will decrease. The Langmuir isotherm takes this into account:

This equation assumes that all adsorption sites are identical, that the probability of a molecule adsorbing is proportional to the concentration of the adsorbate in the fluid and the number of adsorption sites (or surface area) available without adsorbate molecules, and that the rate at which molecules are being desorbed is proportional to the number of adsorbed molecules. The equation for this isotherm involves two constants rather than the single parameter required for the simpler linear isotherm. The shape of the isotherm is illustrated in Figure 5b. Note that the curve is linear for low concentrations (and thus low adsorption), and at higher concentrations the isotherm bends to form, eventually, a horizontal asymptote at high concentrations. The asymptote corresponds to the condition when all of the adsorption sites are filled with the adsorbate. The two constants required to describe a Langmuir isotherm can be written in terms of the

54

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initial slope (at low concentrations) and the horizontal asymptote (&qmax and qmax). Although the Langmuir isotherm is very simple in form, it is not always easily incorporated into rate equations for adsorption bed dynamics. The Langmuir isotherm is based upon a simple and logical basis, but it clearly involves idealizations and approximations and is only an approximate model that cannot be expected to fit more than a few cases. As noted earlier, it does not account for variations in the activity coefficients in either the fluid or the solid with concentration or loading. It also assumes that all adsorption sites or surfaces are identical and not affected by the presence of other adsorbate molecules. These are not good assumptions for all systems.

Other isotherms It is not practical, or even possible, in this volume to describe all of the isotherms and isotherm shapes that can be important to adsorption operations. In some cases, it may be preferable simply to rely upon graphical presentations when data are not adequately described by a well-known isotherm equation. In other cases, it may be possible to use a portion of an experimental isotherm over the concentration range of interest, usually the low concentration region, and fit that portion of the isotherm to a simple equation, even if the data over an extended range clearly cannot be described by the equation. There are many reasons why adsorption isotherms could differ from the relatively simple Langmuir form. Besides interactions between solute molecules, there can be significant variations in the sites on the adsorber itself. It is probably obvious that if an adsorbed molecule attracted more molecules to adjacent sites (or affected the adjacent sites in any way), there would then be more than one type of site. However, even when the solute is adsorbing on the surface of the adsorbent, there could be important differences in the surface. These differences could, of course, result from impurities on the surface, but even clean and uniform surfaces can look different to solute molecules. Remember that most adsorbents used in commercial separations involve pores and surface areas significantly greater than the external surface area of the particles. Furthermore, pore diameters usually vary considerably. Since solute molecules can be affected by all surfaces near the molecule, the adsorption affinity for solute molecules will depend upon the pore size. If all pores do not have the same diameter, the affinity of the solute molecules for the surface will not be uniform.

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The Freundlich equation, = k,d"

(3)

is one commonly used empirical equation which contains curvature much like the Langmuir isotherm that can fit many sets of data. Its simpler form sometimes makes it easier to use than the Langmuir equation (Figure 5 ~ ) . The Freundlich is another two-parameter isotherm. The exponent n is usually less than unity, and then the isotherm has negative curvature and resembles a Langmuir isotherm in general appearance. If data are available only over a limited range of concentrations or pressures and contain the usual experimental scatter, it may not be possible to determine if the data are fit better by a Langmuir or a Freundlich equation. The important differences between the Langmuir and Freundlich isotherms are evident at very low and at very high concentrations. Note that the Freundlich equation does not approximate the linear isotherm at low concentrations. In fact, when n < 1, the initial slope of the Freundlich isotherm is infinite at infinitely low concentrations. Although this is not usually realistic, the Freundlich equation is frequently used successfully when the extremely low concentrations are less important. Note also that the Freundlich equation does not approach an asymptote at high concentrations. This can also be a potential problem if there is a clear maximum adsorbent capacity However, there may not necessarily be a maximum capacity, at least not in the simple sense of the Langmuir isotherm. Multi-layer adsorption can occur, and the clearly defined maximum capacities envisioned by the Langmuir isotherm may not occur. The BET equation is frequently used to describe adsorption equilibria when interactions between adsorbed molecules are important. Adsorbed molecules can increase the probability that additional molecules will be adsorbed. This equation can describe the relative affinity of adsorbate molecules for active sites and for other adsorbed molecules, but it requires more parameters than the Langmuir or Freundlich isotherm equations. It is important to remember that all of the equations used to describe isotherms involve significant assumptions or are entirely empirical. Thus, they are often viewed as approximate descriptions of the real isotherms. Data from real systems need not fit any of these relatively simple equations. To distinguish whether a given set of data agrees with (or is "fit" better by) one isotherm rather than another often requires considerable data taken over a proper range of concentrations, and if the system is not going to be operated over such a wide range of concentrations, the better fit by either equation may not be important. To distinguish the Langmuir

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isotherm from the Freundlich isotherm, one needs data from low concentrations where the Langmuir isotherm has a finite and constant slope (is linear) and/or at high concentrations where the slope of the Langmuir isotherm approaches zero and the curve approaches an asymptote, while the Freundlich isotherm continues to rise and does not approach an asymptote. Of course, it is possible for a real isotherm to have a linear slope at very low concentrations, but no asymptote at high concentrations. Such isotherms will not be fit well over the entire concentration range by either of these simple isotherm equations. One can try the BET equation for such systems. This can be evidence that solute-solute molecular interactions should not be ignored. For most engineering applications, agreement with an equation is important principally because the equation can be used in mathematical models to describe and predict the behavior of adsorption beds. It is, however, important only that the isotherm expression describe the entire range of concentrations that will occur in the adsorption process. For a single solute (adsorbate), the maximum concentration that will occur during the adsorption period will be the concentration of the inlet (feed) fluid, so data at higher concentrations are not necessq. If very high removal efficiencies are required, as they are in many waste management applications, the isotherm will need to be known down to concentrations approaching zero. Remember that at low concentrations, the slopes of Langmuir and Freundlich isotherms can be significantly different. When data are taken principally at higher concentrations where chemical analyses may be more accurate, extrapolation to low concentrations using the wrong equation could cause significant errors (likewise extrapolation to very high concentrations would be risky). The role of the slope of the isotherm on column performance will be discussed later. Here it is sufficient to note that if one is interested in behavior at low breakthrough, accurate representation of the isotherm in that region may be necessary. Some effective use has been made of a hybrid of the Langmuir and Freundlich isotherms. The form of the Langmuir isotherm is retained, but the concentrations are changed to concentrations raised to a power n, much as in the Freundlich isotherm:

This is a three-parameter isotherm. By incorporating the empiricism of the Freundlich isotherm, there is little theoretical (or model) basis for this isotherm, but, if it is useful, it should be considered when needed. For desoprtion, it would generally be desirable to know the isotherm at concentrations that correspond to the maximum loading that

ADSORPTION AND ION EXCHANGE

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occurs during the adsorption period. That is, the isotherm needs to be known to the concentration at the higher temperature (or other difference in adsorption and regeneration conditions) that corresponds to the loading that would be in equilibrium with the adsorbent loaded at the inlet feed concentration at the adsorption conditions. Usually, desorption occurs at significantly different conditions; for gases this is often at higher temperatures or lower pressures. If the isotherm conditions strongly favor desorption, it may not be as common to analyze the desorption step as carefully as the adsorption period. This may be the case in many waste management and environmental applications. However, if energy requirements are high for desorption, if desorption is particularly difficult, or if very high solute removal is needed, it may be necessary to analyze the desorption more carefully, perhaps even more carefully than the adsorption conditions. Remember that some adsorbents, such as activated carbon, may be regenerated “off site,” under relatively high temperatures, and by a commercial desorption service company, not by the user. Multi-component Adsorption Isotherms

Multi-component adsorption is defined as an adsorption process in which more than one solute (adsorbate) is adsorbed. Obviously if there are so many adsorption patterns for single components, there must be far more patterns possible when a number of solutes are involved. Because the potential shapes of multi-component isotherms are so numerous, it is not practical to describe even a significant fraction of the potential isotherm shapes. Even for the experimentalist, multi-component isotherms present practical problems because so much data can be required to describe the equilibria. It may be necessary to describe the isotherm graphically. Here, only one multi-component isotherm and one alternative form will be described-the multi-component Langmuir isotherm:

Note that this equation is a logical expansion of the single component Langmuir isotherm. The subscript i denotes the component of immediate interest. The equation differs from the single component isotherm only in the sum of the product &C for all componentsj rather than accounting only for component i . Thus this equation accounts for the portion of the adsorbent surface occupied by all solutes as well as the solute of immediate interest. The multi-component Langmuir isotherm includes all of the assumptions of the single component isotherm along with two others. First, it

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58

assumes that all of the components adsorb with the conditions assumed in the Langmuir isotherm. Of course, that limits its strict applicability to components that adsorb in this manner, but there are such mixtures. The second assumption is that the total or maximum capacity of the adsorbent is the same for all components. This assumption is contained in the use of the same constant qmaxfor all components. If the adsorption is by surface coverage, this assumes that the coverage per molecule is essentially the same for all components. For some systems, that means that the sizes of the adsorbed molecules are approximately the same and occupy the same adsorbent surface per molecule adsorbed. However, in some cases, adsorption occurs at “active sites” on the adsorbent surface, not on the entire surface. Then the assumption would only imply that all active sites adsorb the same number of molecules of any of the solutes. If a site adsorbs only one molecule, this may not be such a bad assumption. One reason that so much multi-component adsorption data in the literature seem to be described by (or fit by) a multi-component Langmuir isotherm is the moderate number of parameters that are needed to describe the equilibria. Note that if there are n components being adsorbed, one needs to determine n 1 parameters (qmmand n values of ki) to describe the equilibria. Even evaluation of this number of parameters can require considerable experimental measurements as the number of components becomes large. Perhaps the best way to evaluate the parameters and test the multi-component Langmuir isotherm is to measure qmmand ki independently with single component measurement and then test the predicted adsorption with results containing a few multi-component mixtures. Of course, the first signs of difficulty appear if the data for some components do not fit a Langmuir form and/or if the values for q m m are greatly different for the different components. The use of other isotherm equations or graphical representations is likely to require more data. The data needs are made even greater because, in adsorption beds, individual components may adsorb sequentially and be displaced (eluted) by other components. Then the range of concentrations of individual components can vary greatly, and in parts of the beds the concentration of a component can even exceed the concentration of that component in the feed. It is not always easy to predict the range of concentrations that needs to be investigated for mixtures of many components.

+

CLASSIFICATION OF ISOTHERMS The shape of the isotherm strongly affects the behavior of single component adsorption in beds. The adsorbent capacity at the feed concentration

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determines the minimum size of the bed required to remove the adsorbate for a specified period of time. As pointed out in the next section, the curvature of the isotherm usually has the most important (first order) effect on the spreading of concentration fronts that move through a bed of adsorbent particles. Thus, the curvature of the isotherm affects the additional volume or length of the bed required because of front spreading. The isotherms discussed in the previous section should be considered only as examples; they do not cover all isotherms that could be observed in practice. A more generalized classification of isotherms was suggested by Brunauer et al. [ 3 4 ] .They proposed four types of isotherms that describe qualitatively essentially all observed adsorption behavior. These classifications are based upon the curvature of the isotherms, and no particular equations are suggested for any “type” of isotherms. However, we can identify which type includes each of the isotherms discussed earlier. The Brunauer classifications are illustrated in Figure 6. v p e I isotherms are concave downward; they have a negative curvature. That is, d2q/dc25 0 over the entire concentration range. The common equations discussed in the previous section (Langmuir and Freundlich) are both Type I isotherms. This is the most common type of isotherm, especially when the linear isotherm (d2q/dc2= 0)is included in Type I. Although for engineering applications no mechanism is necessarily needed to explain the reasons why an isotherm falls into one type or another, it may be helpful to note that the negative curvature of a Type I isotherm implies that each increment of additional adsorption makes the next increment more difficult (or less likely). This may imply that there is a limited capacity for the adsorbent as assumed in the Langmuir model, and as the solute loading approaches that capacity it becomes increasingly more difficult to add more of the adsorbate. Type I1 isotherms have a positive curvature; they are concave upward. These isotherms are less common than ’Ifrpe I isotherms, and the earlier section gave no equations specifically developed to describe Type I1 isotherms. However, the Freundlich isotherm equation can be made to have such behavior if the exponent n is greater than unity. Although not common, the ?)ye I1 isotherm suggests that adsorption becomes more favorable as more of the adsorbate is adsorbed. That may imply that adsorbed adsorbate molecules have a greater affinity for other adsorbed molecules than for the adsorbent surface. Types 111 and N isotherms have both negative and positive curvatures in different concentration or pressure ranges. v p e 111 isotherms have negative curvatures at low concentrations and positive curvatures at high concentrations, while Type IV isotherms have positive curvatures at low concentrations and negative curvatures at high concentrations.

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C

C FIGURE 6 (a) Class I adsorption isotherm (negative curvature over entire isotherm range). o>) Class I1 adsorption isotherm (positive curvature over isotherm entire range). These changes in the sign of the curvature suggest that there is a change in the nature of the adsorption. The BET isotherm is a 111 isotherm. At low concentrations adsorbate molecules are adsorbing largely on the adsorbent surface, but at higher concentrations the adsorption approaches a monolayer of adsorbed molecules, and further adsorption takes place largely on other adsorbed molecules, perhaps even filling the pores of the adsorbent. Note that at low concentrations Type I11 and Type IV isotherms can appear much like I and Type I1 isotherms, respectively.

me

me

ADSORPTION AND /ON

67

EXCHANGE

C

FIGURE 6 (c) Class 111 adsorption isotherm (negative curvature at low concentrations and positive curvature at higher concentrations). (d) Class lV adsorption isotherm (positive curvature at low concentrations and negative curvature at higher concentrations).

ION EXCHANGE EQUILIBRIUM The exchange of ions between an ion exchange material and a solution can be described as follows: 1 1 -[My'] + -&I n2

1

2 -[[MI] n1

1 + -[MfnZ] n2

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CHAPTER 2

This expression describes the cation exchange of one metal ion in solution (MI) for another metal cation within the resin (M2).The valences of the two ions are nl and n2, respectively. The underscore signifies that the ion is in the resin phase. This relation is sometimes written to look as if a chemical reaction is taking place with one ion in solution replacing an ion attached to the resin, but the formulation in (6) is preferred because it does not imply that ions in the resin are associated with any resin site. It is better to think of the resin and the solution as different phases. Although this equation was described in terms of cation exchange (all exchanging ions having positive charges), the valences could be negative, and the equation would then describe anion exchange. Equilibrium can be written in terms of the mass action equation:

K is an equilibrium “constant” that includes effects of the activity coefficients for both ions in both the aqueous and resin phases. If the activity coefficients are constant, then K is truly a constant. Otherwise, there will be some variation in K with solution or resin composition. In many cases, there will not be a large variation in activity coefficients over operation conditions, but one should take care when assuming a constant value of K ,especially if a wide range of solution compositions is of interest. This equation is written in terms of the ratio of the concentration of ion 1 in the resin to its composition in the solution. In describing adsorption equilibrium, this ratio was referred to as the “distribution coefficient.” Note that for the simple exchange of two ions, the distribution coefficient of one ion is approximately constant only if the distribution of the other ion is approximately constant. During an operation when one ion is loading on the resin and another ion is being displaced, neither of these ratios will be approximately constant, even for dilute solutions. Do not assume that at dilute concentrations ion exchange equilibria will be like linear isotherms in adsorption systems. One should not expect a constant distribution coefficient (that is, a linear isotherm) for ion exchange, even from dilute solutions. The possible exception occurs when the ion of interest is dilute, but the other ion is concentrated in both the solution and the solid. Then the solution and the resin would remain largely loaded with the other component, so the distribution of the trace component could be approximately constant as the concentration of the trace component increases. Another mistake that appears to be common is to assume that a dilute ion exchange system can be approximated by a Langmuir isotherm (or, as just mentioned, even a linear isotherm). There is an important

ADSORPTION AND ION

EXCHANGE

63

difference in ion exchange and adsorption because even in a dilute system, a column initially saturated with component 2 can be completely loaded with sufficiently large volumes of even the most dilute solution of component 1. The resin will be saturated with component 1 regardless of the concentration. It is clear that it cannot be approximated well with a linear isotherm at low concentrations. The effective curvature in the isotherm (if one wants to think of ion exchange equilibrium in terms of an isotherm) depends upon the change in the ratio of concentrations of ions 1 and 2 in the solution and resin, not upon the actual concentration of either ions 1 or 2. There are similarities and differences between ion exchange equilibria and Langmuir isotherms that will be discussed in the next section. Preferences of most polymer gel-type resins for different ions usually can be conveniently grouped as first order effects, based upon the valence (charge) of the ion, and second order effects, or special affinity of some ions for the resin phase. In only a few cases will these second order effects be as important as, or more important than, first order valence effects. The valence effect can be illustrated by using Equation (7)to calculate the separation factor for two ions between the resin and solution. The separation factor is the ratio of the distribution coefficients:

Note that [M2] > [M2] because the resin capacity is greater than the solution concentration (at least for dilute solutions), and [Mz]/[Mz] > 1 (usually [M2]/[M2] >> 1).When the two ions have the same valence, n1 = n2, the exponent on the right side is zero and the separation coefficient is equal to K. In that case, there is no valence effect. The separation factor then is equal to K and reflects only second order activity effects. However, when tz2 > n1, the exponent is positive and the separation factor is greater than unity unless the activity terms make K small enough to compensate for the valence effect. This is the case when an ion with a lower valance, n l , is displacing an ion with a higher valance, n2.This means that the resin favors the cation with the higher valence. For dilute solutions where [M2] >> [Mz], the resin may favor the higher charged ions strongly. Similarly, when n2 < n l , the exponent is negative and the resin favors ion 1 over ion 2 and still favors the ion with the higher charge. Thus, most resins prefer to lose single charged ions, such as sodium or potassium ions, and gain ions from the solution, such as calcium or magnesium, that have double charges. When loading a resin with doubly charged ions such as calcium and regenerating with singly charged

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ions such as sodium or hydrogen, it is better to regenerate with high concentrations where the preference for the doubly charged ion will not be as great. Second order selectivity can come from general behavior that follows a pattern for many ion exchange materials, or it can be specific for a few ions and a few resins. The “general” effect probably results because the interior of an ion exchange resin contains sufficient organic polymer that it is usually not very hydrophilic, despite the fact that the ionizable groups on the resin do bring large quantities of water into the polymer. This usually results in a selectivity for the less hydrophilic ions in each series, those ions that bring Less water into the resin. For instance, in the alkali metal series, cesium is usually the most preferred ion in the series and lithium the least preferred. In most such series, the ions with the largest size (or molecular weight) are preferred by the resin, and they are usually the ions with the least waters of hydration. The degree of selectivity for ions in such a series can be altered by changing the organic content and type of organic components in the polymer. Perhaps the most common examples where specific interactions or “second order” activity effects are extremely important are the weak acid cation exchange materials and weak base anion exchange materials. Weak acid resins can have strong affinities for hydrogen ions, and weak base resins can have high affinities for hydroxyl ions. Other ion exchange groups may show considerable preference or affinities for other specific cations or anions, but these effects are usually not as strong or as common. Although these special affinities may be important for selected applications, only a few resins have preferences for specific ions that are sufficient to overcome the valence effects. Some of the other specific selectivities can result when a resin contains a group that interacts strongly with a specific cation, but that group may not be part of the ion exchange function. For instance, some ion exchange resins that contain thio-sulfur have high selectivity for mercury ions or for ions of most metals that form highly insoluble sulfides. Some selectivities resulting from these effects can be significant.

Comparison of Ion Exchange Equilibria and the Langmuir Isotherm The relation between ion exchange and Langmuir adsorption can be illustrated best by considering exchange of ions with the same valance (nl = n2 = n). Then the equilibrium loading of the first ion can be written as

65

ADSORPTION AND ION EXCHANGE

since C = nlMl+ n2M2

and

C = nlMl + n2M2

(That is, the total concentration of ions in the solution C , and the total concentration of ions in the resin C, is not changed by the exchange of ions.) Then

Here the concentrations in the resin and the solution are normalized by the total concentration of cations (or anions for anion exchange) in the resin and solution, respectively. Thus, the concentrations represent the fraction of the resin capacity and the fraction of the solution cations occupied by the reference ion, component 1. The loading of component 1 in the resin occurs in both sides of this equation; therefore, to get this into a form similar to the Langmuir form, the equation must be solved for Ml/(C/n). Then

Note that this resembles the Langmuir isotherm equation, but there are two important differences. First, the concentrations are expressed in terms of the fraction ions that are component 1, not in terms of the absolute concentrations of component 1. Next note that the coefficient for the second term in the denominator of the right-hand side is K - 1 not K, as one would expect if the form of the equation were to be just like the Langmuir isotherm equation. When the exchanging ions have different charges, there is even less similarity with a Langmuir isotherm. In such cases, it is usually not helpful to compare the ion exchange equilibria with the Langmuir isotherm.

Measuring Ion Exchange Resin Parameters To evaluate the equilibrium parameters, it is usually easier to determine the resin capacity by titration of the hydrogen form of the resin (or hydroxyl form of an anion resin) with a base (or acid for an anion resin),

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66

or to saturate the resin with any ion that can be easily analyzed, elute it with a large volume of another ion, and analyze the eluate. The equilibrium constant for a binary system can be evaluated by equilibrating the resin with different concentrations of the two ions of interest and analyzing. Often it is only necessary to analyze for one component and to determine the final concentration and resin loading for the other component by difference, provided changes in solution concentrations are large enough to determine the differences accurately. If a graphical determination is desired, a log-log plot of &/MI versus M2/M2 should give a slope of n 1 / n 2 , and the position of the line will give the value of K . If the data fall along a straight line with the proper slope, that is evidence that the simple ion exchange mass action equation [Equation (31that assumes approximately constant activity coefficients is appropriate. Then K will be the value of M l / M 1 when M2/M2 = 1. The fit of the data to a smooth curve with approximately the expected slope provides an indication of the scatter or uncertainty in the data as well as the accuracy of the assumption of constant activity coefficient, that is, a constant value for K. Note that when the valences of the two ions are the same, one can make a plot much like that usually used to evaluate the Langmuir constants. From the last equation, one can find that a plot of l/M1versus C/nM1 should give a straight line with n slope = KC

and intercept =

n(K - 1 )

KC

This lets one use the analogy to a Langmuir isotherm, but note that the parameters K and C appear in both the slope and the intercept. However, it is not difficult to evaluate the parameters since K = l +

intercept slope

When the two exchanging ions have different valences, there is no convenient way to use the Langmuir-like graph. Multi-component Ion Exchange Equilibrium

Since ion exchange operations require at least two ions (one displacing the other on the resin), multi-component ion exchange refers to situations

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/ON EXCHANGE

67

with three or more cations (or anions). Multi-component ion exchange can be viewed as a series of individual binary exchanges, and Equation (7)can be applied to each pair of ions. If there is a total of m cations (or anions for anion exchange) in a solution equilibrated with a cation exchange material, there will be m - 1independent forms of Equation (7) to describe the binary equilibrium, or m - 1values of K to be determined. Since there are m concentrations in the resin to be determined from the equilibrium relations, one other independent equation is needed, the total cation balance:

where R is the total capacity of the resin. Note that penetration of anions into the resin and change in activity coefficients with solution concentration and composition have been ignored. For most dilute solutions, this is a good approximation. If the resin has a particularly strong affinity for one or more of the ions present, the Ks may show more change with composition. If anion penetration is significant (for cation exchange), an equivalent number of cations must be added to the cation balance in the resin. In principle, multi-component ion exchange can be predicted from a series of m - 1 binary measurements, which for many systems gives satisfactory results. As noted, however, there are situations and factors that could cause inaccuracies in such an ideal approach. There are numerous ways to evaluate multi-component ion exchange equilibria, and readers can choose the approach that is most suitable for their problems. However, this author prefers to see the m - 1 binary equilibria constants evaluated, and it is usually easier to evaluate those parameters by using binary exchange measurements. Of course, if those parameters remain constant in the multi-component systems, those are the only parameters needed except for the exchange capacity of the resin. However, it is wise to check this by making at least a few multi-component equilibria measurements to be sure that the multi-components measurements can be predicted reasonably accurately with the parameters determined from binary measurements. It will be most appropriate to make the multi-component measurements with concentrations as close as possible to the concentrations expected in the operating system. In some respects using this simple extension of the binary exchange to predict multi-component equilibrium is much like using the multicomponent Langmuir equilibrium equation where parameters obtained from single component data and some of the factors that could cause problems in the expansion to multi-component situations are similar

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for both situations. For instance, interactions between the ions in either phase could cause significant error in the ideal treatment just described. Nevertheless, as with multi-component adsorption, considerable equilibrium data are required to describe multi-component systems even using idealized equations, and it is desirable to search for simple approaches such as this to minimize the data needed. More elaborate and accurate relations usually require even more data, so the simpler relations are likely to be used, or at least tried first. As noted, when idealized equilibrium relations are used, it is best to check the results at conditions as near as practical to those that will be used. To minimize the effects of deviations from the ideal approach, it may even be advisable to make the binary measurements at conditions as near to those expected in the application as practical. Generally this will mean measurements at the same normality as the feed solution. Since ion exchange involves exchange of equal equivalents of ions between the solution and resin, there is no net change in the normality of the solution during batch equilibration or as solutions pass down an ion exchange bed; only the composition of the solution changes. The actual feed composition is one concentration that should be tested, but one should be aware that in multi-component systems, a great variety of compositions could develop at different positions in an adsorption bed. This is as true for ion exchange as it is for adsorption.

Co-Ion Penetration and the Donnan Effect When ion exchange is used in waste management operations, the concentration of the ion to be removed from solution is usually low. However, the concentration in the resin will not be low. The concentration of metal ions in the resin is set largely by the resin capacity and will be essentially independent of the solution concentration. The total Concentration of cations in a cation exchange resin is

R is the concentration of ion exchange groups (anion groups for cation

resin and cation groups for anion exchange resins) attached to the resin polymer, and C, is the normality of electrolyte anions that diffuse into the cation resin from the solution (or cations that diffuse into an anion resin). For high capacity polymer-based ion exchange materials, R is normally between 2 and 5 molar. Since that concentration is much higher than the concentrations in most dilute wastewaters treated by ion exchange, one would not expect the penetrating electrolyte concentration C, to

ADSORPTION AND /ON

EXCHANGE

69

contribute significantly to the total concentration of exchanging ions in the resin. Actually, anions are excluded from cation resins (and cations are excluded from anion resins) by Donnan exclusion; hence, the concentration of solution anions in a cation resin is much less than the concentration in the external solution. This effect can be explained by considering a solution of a single salt (cations and anions) in equilibrium with a cation resin. Of course, if there is only one salt in the external solution, the resin contains only one cation, that of the salt. Note that at equilibrium the activity of the salt must be the same in the solution and in the resin. Then, neglecting activity coefficients (assuming first that the activity coefficients are approximately the same in both phases), n l n, n tl] 1 [c-ncln' = [MI - 1 [c-"I

[ ~ ' 1 1 nc

1

(17)

where C is the anion and nc is the (negative) charge of the anion. Writing this in terms of the distribution coefficient for the anion gives

For dilute solutions [MY']